AN ENVIRONMENTAL EVALUATION

OF THE

LOWER WELLAND RIVER

JULY 1993

@ Ontario

Ministry of
Environment
and Energy

ISBN 0-7778- 1644-X

AN ENVIRONMENTAL EVALUATION
OF THE LOWER WELLAND RIVER

JULY 1993

0

Cette publication technique
n'est disponible qu'en anglais.

Copyright: Queen's Printer for Ontario, 1993

This publication may be reproduced for non-commercial purposes

with appropriate attribution.

PIBS 2659

AN ENVIRONMENTAL EVALUATION
OF THE LOWER WELLAND RTVER

Report prepared by:

R.J Pope, K.A Keenleyside, S.D Speller
Tarandus Associates Limited

for

The Niagara River Improvement Project
Ontario Ministry of the Environment

JULY 1993

DISCLAIMER

The content and conclusions of this report do not
necessarily reflect the views and policies of the
Ontario Ministry of Environment and Energy. The
data as presented are regarded as valid and can be
used in additional assessments.

Mention of trade names or commercial products
does not constitute endorsement or recommendation
for use.

Executive Summary

An environmental evaluation of the lower Welland River was conducted by Tarandus Associates
Limited during the summer and fall of 1990. The study involved an assessment of water and sediment
quality, as well as an examination of aquatic flora and fauna.

The objectives of the study were:

1) to obtain a database subset for the lower Welland River for use in assessing
possible remediation options where appropriate and for determining the need
for further environmental investigations and;

2) to provide information for use in evaluating the significance of the Welland
River regarding environmental quality issues in the Niagara River Area of
Concern.

After an initial reconnaissance of the study area, field trips to the lower Welland River were completed
during August and November, 1990. A total of 25 stations were evaluated. Analyses of sediments
and water from these stations were conducted by Beak Analytical Laboratories.

Water quality varied considerably among stations. At several sites, iron, copper, mercury, and total
phosphorus exceeded the Provincial Water Quality Objectives (PWQO). Most water-quality
parameters, however, including most metals, phenols, total cyanide, PCBs, polyaromatic hydrocarbons
(PAHs), and organochlorine (OC) pesticides were below detection limits.

Data from regular MOE water-quality monitoring stations indicate that levels of zinc, copper,
mercury, chromium, and lead have decreased in the Welland River from 1979 to 1987. A slight
increase in aluminum concentrations in water, however, has been noted from 1981 to 1987.

Sediment quality was also variable throughout the study area. Concentrations of lead, chromium,
mercury, cadmium, zinc, iron, nickel, copper, arsenic, total Kjeldahl nitrogen, total organic carbon,
total phosphorus, and PCBs exceeded the MOE Provincial Sediment Quality Guidelines (PSQG) lower
effect limit (LEL) at some stations." The PSQG - Severe Effect Limits (SEL) for chromium, mercury,
nickel, iron, and copper were also exceeded at several stations in sections B and C of the study area.
Concentrations of total cyanide and oil and grease exceeded the Open Water Disposal Guidelines
(OWDG) at some stations. PAHs were also detected at several stations, most notably stations 9 and
10. All organochlorine pesticides were below detection limits.

Degraded sediment quality, as indicated by concentrations of several metals, oil and grease, total
cyanide, and PAHs were found at stations 9, 10, 24, 11, and 12, in the lower Welland River between
the syphons, as well as at stations 17, 18, 19 and 20 in the section east of Port Robinson. Sediments
at station 7, located in the western portion of the City of Welland also had elevated concentrations of

several contaminants. A number of contaminant inputs are located in the vicinity of these stations,
including storm sewers, a landfill site, a water pollution control plant (WPCP), and several industries.

Ninety benthic-invertebrate taxa were identified at the 25 sampling stations. The total is significantly
higher than the 28 taxa reported previously (Johnson, 1964). The number of taxa varied among
stations, rajiging from a low of 12 species at stations 6 and 25 to a high of 29 species at station 10.

Two invertebrate species were common to all the sampling stations; Procladius sp. and immature
tubificids, although Chryptochironomus sp. , Limnodrilus hoffmeisteri , and Sphaerium sp. were found
at 24 of the 25 sites. Johnson (1964) also noted Procladius and Limnodrilus throughout the Welland
River. Sampling stations located upstream of the City of Welland were characterized by relatively
high numbers of Hexagenia sp. and Coelotanyus sp. These species were generally absent from
stations downstream of Welland, indicating degraded environmental conditions. Stations located below
the urbanized areas were characterized by relatively high numbers of the more pollution-tolerant taxa,
Spirosperma ferox and immature tubificids, as well as Valvata sp., and Hydrobiidae.

The total abundance of benthic invertebrates varied among stations in the study area, and ranged from
a low of 634 individuals per square meter at station 12 to a high of 5900 individuals per square meter
at station 22. Generally, stations located in and below the City of Welland had higher total
abundances than those located in the rural area above Welland.

Benthic-invertebrate diversity (Shannon-Weaver and Brillouin) fluctuated considerably, especially in
the river below the City of Welland. Diversities at all the stations upstream of Welland were
relatively constant, ranging from 3.02 to 3.53. Shannon diversities ranged from a high of 3.96 at
station 1 1 to a low of 2.52 at station 25. Similar trends were noted with the Brillouin diversity index.
Diversities greater than 3.0 are generally indicative of unpolluted conditions.

Discriminant analysis of the stations, based on the results of cluster analyses, indicated that benthic-
invertebrate communities below the City of Welland and above the Queenston-Chippawa Canal were
associated with sediments characterized by elevated concentrations of several metals including
chromium, copper, and arsenic. In contrast, benthic communities at stations above the City of
Welland, occurred in an area characterized by sediments having relatively low levels of metals, and
a high loss on ignition. Aluminum was also found at higher concentrations in this part of the Welland
River than at stations further downstream.

The fish community of the lower Welland River was dominated by warmwater species, including
catfish, white crappie, carp, suckers, and freshwater drum. Salmonid species were not found in the
lower Welland River, although they are common in the Niagara River.

The Welland River shoreline was dominated by several emergent aquatic macrophytes, including
Typha latifoUa and Sagiitaria laiifolia. A number of submerged aquatic macrophytes were also noted
including Myriophyllum spicamm, Vallisneria americana, and Ceratophyllum demersum. These
species have been previously reported in the study area by Johnson (1964) and Dickman et al. (1983).
Previous authors have also noted areas devoid of higher aquatic plants below several industrial
discharges (Dickman and Haynes, date unknown; Dickman eral, 1983). During this study, sparse
macrophyte growth was only noted below the Thompson's Creek confluence.

Table of Contents

Page

Executive Summary i

List of Tables • v

List of Figures viii

List of Appendices x

Introduction 1

Study Methods 3

The Study Area

Water Quality 5

Sediment Quality

Benthic Invertebrates

Aquatic Macrophytes

Fisheries 9

Flow Measurements 10

Statistical Analyses H

1) Indices H

i) Shannon-Weaver Diversity Index 11

ii) Brillouin Diversity Index 12

2) Cluster Analysis 12

3) Principal Components Analysis 13

4) Discriminant Analysis 13

Results and Discussion 15

Water Quality 15

Sediment Quality . 27

Benthic Invertebrates 44

Table of Contents (continued)

i) Species Composition, Abundance, and Diversity 44

ii) Benthic Community Classification 51

iii) Environmental Quality Evaluation 54

Fisheries 60

Aquatic Macrophytes 62

Flow Measurements 64

Conclusions .65

Water Quality 65

Sediment Quality 65

Benthic Invertebrates and Environmental Quality 66

Fisheries 67

Aquatic Macrophytes 67

References 69

List of Tables

Table Page

1 The four sections of the study area 5

2 Analytical parameters - water 6

3 Analytical parameters - sediment 7

4 Sediment-quality parameters evaluated during the fall surv 8

5 Sediment-quality parameters used in discriminant analysis 14

6 Water-quality parameters below detection limits in all the

Welland River water Samples

7 Polycyclic aromatic hydrocarbons and their associated detection limits 23

8 Organochlorine pesticides and their associated detection limits 24

8b MOE results for concentrations of chlorinated organics in water

at stations 6 and 21. 25

9 A comparison of the water-quality of the Welland River with

selected river systems in the area 27

10 Provincial Sediment Quality Guideline levels and their significance 28

11 Concentrations of PAHs in Welland River sediments collected

during the summer survey 33

List of Tables (Continued)

Table Page

12 Concentrations of PAHs in Welland River sediments collected
during the fall survey

34

12 b MOE results for concentrations of chlorinated organics at ^

sites 6, 9, 15 and 21. 35

13 Organochlorine pesticides and associated detection limits in sediment 38

14 Summary of sediment quality at all stations based on the PSQGs 40

15 Comparison of selected sediment-quality parameters at station 9 41

16 Comparison of selected parameters in sediments collected offshore

of the Atlas outfall . 41

17 A comparison of Welland River sediments with sediments from

Thompson's Creek, Lyon's Creek, and the Niagara River. 43

18 Number of taxa, total abundance, and diversity (Shannon and Brillouin)

for all stations 50

19 Correlations between the sediment parameters and the first two

discriminant functions for the benthic-invertebrate communities 56

20 Mean concentrations of the sediment parameters associated with the

benthic-invertebrate communities 56

21 Correlations between the sediment parameters and the first two
discriminant functions for the three benthic communities in the
Welland River 59

List of Tables (Continued)

Table , Page

22 Fish species caught in the Welland River during the summer and fall survey 61

23 Numbers of fish caught in hoop-net sets in sections A, B, and C 62

24 Species of submergent and emergent aquatic macrophytes found in the

study area during the summer survey 63

List of Figures

Figure Page

1 Welland River study area 2

2 Welland River sampling locations 4

3 Concentration of zinc, copper, chromium, mercury, and lead

in water samples collected at the Montrose Bridge from 1979 to 1987 18

4 Aluminum concentrations in water samples collected at the Montrose

Bridge and Port Robinson from 1981 to 1987 19

5 Total phosphorus levels in water samples collected at the Montrose -

Bridge, Port Robinson, and the Welland Airport from 1979 to 1987 20

6 Mean-yearly TKN levels in water samples collected at the Montrose

Bridge, Port Robinson, and the Welland Airport from 1979 to 1987 22

7 Tubificid abundances 45

8 Chironomid abundances 46

9 Hexagenia abundances 47

10 Total Oligochaete abundances 49

11 Cluster analysis results using Euclidean distance and Ward's method 52

List of Figures (Continued)
Figure Page

12 PCA results of benthic-invertebrate abundance 53

13 Plot of benthic-invertebrate communities in discriminant space as defined by

the first two discriminant functions 55

14 Plot of the Welland River benthic-invertebrate communities in discriminant

space as defined by the first two discriminant functions 58

List of Appendices

Appendix Page

I Water Quality Graphics 73

II Sediment Quality Graphics 81

III Field observations of conductivity, dissolved oxygen,

and water temperature during the fall survey 97

IV Benthic-invertebrate species list 101

V Benthic-invertebrate species counts 107

VI Benthic-invertebrate species abundances 129

VII Taxonomic composition of benthic communities 139

VIII Component loadings for the PCA 145

IX Fish species found in the study area 149

X Flow calculations for sections A, B, and C 153

XI Water Quality Data 157

XII Sediment Quality Data 165

Introduction

In July, 1990, Tarandus Associates Limited was contracted by the Ontario Ministry of the
Environment (MOE) to complete an environmental evaluation of the lower Welland River
(Figure 1). The study included an assessment of water and sediment quality, as well as an
evaluation of aquatic flora and fauna.

The objectives of the study were:

1) to obtain a database subset for the lower Welland River to allow assessment of
remediation similar to that presently underway for the Niagara River as well as to
determine the need for further environmental investigations and;

2) to provide information for use in evaluating the significance of the Welland River
regarding environmental quality issues in the Niagara River Area of Concern.

A number of environmental studies have been completed on the Welland River, including
sediment and water quality assessments (Kaiser and Comba, 1983; Brindle etal. , 1988; Johnson,
1964; Hart, 1986; Acres, 1990), fisheries studies (Johnson, 1964; Steele, 1981), benthic
invertebrate surveys (Johnson, 1964), and aquatic-macrophyte surveys (Dickman et al., 1980;
Dickman e[ al, 1983; Dickman and Hayes, date unknown). Much of the information in the
earlier studies is appropriate only for historical purposes, given that the discharges to the river
have changed significantly in recent years.

Twenty six years ago, Johnson (1964) concluded that domestic sewage and industrial wastes led
to serious water quality impairment in the lower Welland River. More recently, a number of
sources of contaminants to the Welland River have been identified and investigated. Industrial
sources include Atlas Specialty Steels, Cyanamid Canada Inc., B. F. Goodrich and Ford Motor
Company. Various municipal sources such as the Welland Water Pollution Control Plant
(WPCP), and a number of combined sewer outfalls and overflows also exist (NRTC, 1984).

Study Methods

The Study Area

The Welland River is approximately 70 kilometres long, and extends from just south of
Hamilton to the Queenston-Chippawa Power Canal. The section of the Welland River from
Chippawa westwards to the Queenston-Chippawa Power Canal is 6.4 km long and is locally
known as Chippawa Creek. This portion of the Welland River now flows westerly carrying
Niagara River water to the power-canal delta where it mixes with Welland River water and
proceeds down the Queenston-Chippawa Power Canal. The Welland River drains an area of
approximately 906 km' and has an average gradient of three feet per mile to the Chippawa-
Queenston Power Canal. The Welland River is not navigable where it flows beneath the old and
new Welland Ship Canals by way of inverted syphon systems.

The study area extends from O'Reilly's Bridge, which is located south of the Welland Airport,
to the lighthouse in King's Bridge Park at Chippawa, excluding the Queenston-Chippawa Power
Canal. The study area was separated into four sections: A, B, C, and D (Table 1) based on
access, the various land uses, and the nature of developments in each section (Figure 1).

A total of 25 stations were selected for water and sediment analyses, and benthic-invertebrate
collections (Figure 2). Fish were sampled at three net-set locations. Station locations were
selected in consultation with MOE personnel. Sampling intensity was increased in sections B
and C where industrial and municipal discharges are more common. Sampling was reduced in
section A, where agricultural land uses are predominant, and in section D, where the flow
consists of Niagara River water exclusively. The field work for this project was completed
during the periods of August 20th to the 24th, 1990, and November 6th to the 9th, 1990.

Table 1 : The four sections of the study area.

Section (See Fig. 2)

General Description

A - O'Reilly's Bridge to the old Welland Canal

limited residential
predominately rural
agricultural activities common

B - old Welland Canal to the new Welland Canal

mostly residential

several municipal discharges

several industrial discharges

water diverted from the old Welland

Ship Canal

C - the new Welland Canal to the power canal

D - the power canal to the Niagara River

predominately rural
several industrial discharges

Niagara River water diverted to
the power canal through this section
predominately rural

Water Quality

Water samples were collected at all stations with the use of a Van Dorn water-sampler. Each
station sample was a composite of water taken at a depth of 1 meter below the surface at three
locations: from the middle and from both sides of the river. All samples were placed in the
appropriate labelled containers and were preserved as necessary. Samples were stored in a
cooler on ice, until delivery to the laboratory for chemical analysis.

Water samples were collected from all 25 stations between August 20th and August 24th, 1990.
These water samples were analyzed for either an "extensive list" or an "indicator list" of
parameters (Table 2). Samples from stations 1, 9, 15, 21, and 23 were analyzed for the
"extensive list" of parameters, and the remaining 20 stations were analyzed for the "indicator
list". Water temperature, dissolved oxygen, and pH were determined in the field at all stations.

Table 2:

Analytical parameters
in Appendix XI.

water. A glossary of parameter abbreviations is presented

Extensive List

Indicator List

Metals

Pb, Zn, Cd, Cr, Fe,
Se, As, Sb, Ba, Be,
Co, Cu, Mo, Ni, V,
Ag, Hg, CN, Mn, Mg
Al

Pb, Zn, Cd, Cr, Cu
As, Hg, CN, Al

Organics

PCB/OC pesticide scan
PAHs, Phenolics

PCB/OC pesticide scan
Phenolics

Nutrients

NH4, TP, TKN, NO., NO3

TP, TKN

Miscellaneous

pH, conductivity,
dissolved oxygen
turbidity, colour,
suspended solids
temperature

pH, conductivity,
dissolved oxygen
turbidity
temperature

A second set of water samples was collected from all stations during the period of November
6th to the 9th, 1990. All of these water samples were analyzed for phenolics. Water samples
from stations 1-10, 15, 21, and 23 were analyzed for aluminum and copper, and samples from
stations 1-5, 10, 15, 21 and 23 were analyzed for mercury. Water temperature, conductivity,
and dissolved oxygen measurements were determined in the field, at most stations. Dissolved
oxygen depth-profiles were also taken at some stations.

All water analyses were conducted by Beak Consultants Limited according to standard analytical
methods approved by MOE. In addition, water samples were collected from stations 6 and 21
for subsequent analysis at the MOE laboratory in Rexdale. Chemical parameters included
volatile organics, extractable organics, and organochlorine pesticides.

Spatial and temporal trends in water quality were examined throughout the study area. Data
from previous studies, when available, were also incorporated in these analyses. Water-quality
results were compared to the MOE Provincial Water Quality Objectives (PWQO) where
.possible, and to the water quality of other river systems in the area.

Sediment Quality

Surficial sediments were collected with a stainless-steel ponar grab sampler, and consisted of
composites of three sub-samples taken at the middle and both sides of the river. All sediment
samples were homogenized and placed in appropriate labelled jars. Miscellaneous observations
regarding sediment texture and colour, as well as the presence of any odour or oily sheen were
also recorded where evident.

Sediment samples were collected at a total of 25 stations during the period of August 20th to the
24th, 1990. Samples from stations 1,9, 15, 21, and 23 were analyzed for an "extensive list"
of parameters, and the remaining 20 samples were analyzed for an "indicator list" (Table 3).

A second set of sediment samples was also collected during the November survey. A modified
set of chemical analyses based on the results of the August survey was conducted on each of
these samples (Table 4).

Table 3: Analytical parameters - sediments

Extensive

Indicator

Metals

Pb, Zn, Cd,.Cr, Fe,
Se, As, Sb, Ba, Be,
Co, Cu, Mo, Ni, V,

Ag, Hg, CN, Mn, Mg
Al

Pb, Zn, Cd, Cr, Cu
As, Hg, CN, Al

Organics

PCB/OC pesticide scan
PAHs, Phenol

PCB/OC pesticide scan
Phenol

Nutrients ' TP, TKN, TOC, LOI LOI

Miscellaneous pH, SAR, Oil and Grease pH, Oil and Grease

Table 4: Sediment-quality parameters evaluated during the fall survey.

Parameter(s)

Stations

Zn, Cd, Mn, Co, Cu,

Total Cyanide (CN)

Mercury (Hg)

Arsenic (As)

PAH Scan

PCB

Oil and Grease

Fe,

Pb,

Cr,

Ni

5-19,20

17-22

7-13

7-10,11-20

1,3,5,7-10, 15

1, 3, 5, 7-10, 15, 19a, 21, 23

1-23

All sediment analyses were completed by Beak Consultants Limited according to standard
methods approved by MOE.

In addition, sediments were collected from stations 9, 15 and 21 at the request of MOE for
subsequent analysis at the MOE laboratory in Rexdale. Parameters determined included volatile
organics, extractable organics, organo-chlorine pesticides, and dioxins.

Trends in sediment quality were examined throughout the study area. Data from previous
studies, when available, were also used for these analyses. Sediment-quality results were
compared to Provincial Sediment Quality Guidelines (PSQG), and to the sediment quality of
other local river systems such as Thompsons Creek, Lyons Creek and the Niagara River.

Benthic Invertebrates

Benthic-invertebrate samples were collected from the middle and both sides of the river at each
of the 25 stations in August, for a total of 75 samples. All samples were collected with the use
of a ponar grab sampler, and the sediments were sieved through a 200-u mesh sieve-bucket.
Residual materials were placed in appropriately labelled jars, and preserved in 10% buffered
formalin.

All samples were manually washed, picked, and sorted to separate all organisms from associated
debris. All samples were picked in their entirety with the use of a stereomicroscope. The
organisms found in each sample were sorted into similar taxonomic groups and placed in
separate labelled vials for subsequent identification.

All benthic invertebrates were identified to the lowest practical taxonomic level by Dr Richard
Vineyard and Mr Brad Hubley of the firm Original Insect Ideas. Prior to identification,
tubificids and chironomids were cleared and mounted on labelled microscope slides with the use
of polyvinyl lactophenol. In cases where the immature forms of some invertebrates prevented
identification to species, classification was usually completed to the genus level.

All sorted invertebrate samples were provided to MOE at the completion of the project. In
addition, a reference collection was prepared for use in confirming identifications and to ensure
the repeatability of the benthic invertebrate classification in future studies. Slides were labelled
with species identification, date, location, taxonomist and station.

All species counts were tabulated by sample and station, and were converted to abundance counts
(number/m^) for use in subsequent statistical analysis.

Aquatic Macrophytes

A visual qualitative assessment of the aquatic-macrophyte community was completed at all
stations in the study area. Assessments of both submergent and emergent macrophytes were
completed, including observations regarding species present, dominant species, and the presence
of any unusual or rare plants. Photographs of existing aquatic-macrophyte communities in the
study area were also taken where possible to supplement the community descriptions.

A species list of aquatic macrophytes was prepared for the study area. Trends in species
composition and species association were noted, and any atypical occurrences were recorded.
Unusual community patterns, particularly those that may result from anthropogenic disturbances
were also described.

Fisheries

Fish were collected during both field trips to evaluate community composition in the study area.
A Scientific Collector's Fish Permit was obtained from the Ministry of Natural Resources in
Fonthill before the field work for the fish survey was initiated.

Sampling methods included the use of hoop nets, a seine net, and minnow traps. The identity
of all species sampled during the survey was recorded, and any observations of abnormalities,
disease, or parasites were noted. All fish were released alive if possible.

The hoop nets used during the study had a rectangular opening of approximately 47 by 38 inches
(190.5 by 96.5 cm) and hoops measuring about 36 inches (91.4 cm) in diameter. The hoop-net
enclosure measured approximately 20 feet (6.1 m) in length, and had an attached lead of 100
feet (30.5 m). At all sets, the lead was attached to trees or rocks at the shore, and the trap was
positioned in deeper water at an angle that varied from about 45° to 90° to the shoreline. Water

depths in which the hoop net was set ranged from 1.0 to 2.5 meters. This fish survey was
intended to provide general overview information only and was not designed to be a detailed
assessment of the fish populations in the Lower Welland River.

A total of 5 hoop-net sets were completed during the summer and fall surveys. The hoop net
was set once in sections A, B, and C during the August survey and once in sections A and C
during the November survey. Each hoop-net set was placed overnight for a period of
approximately 24 hours. All net-set locations are illustrated in Figure 2.

Fish were also collected with the use of a 5-meter beach seine at a number of locations in
sections A, C, and D during the August survey. The steep banks of section B prevented the
completion of any seining in that part of the river.

A total of 8 minnow traps were also set in sections A, B, and C. The traps were baited with
bread and set overnight.

Flow measurements

Water velocity was measured with the use of a Montedoro-Whitney portable velocity meter at
5-meter intervals across several sections of the river. Velocity measurements were taken at 0.2
and 0.8 times the water depth at each measuring point as recommended by Arseneault (1976).
Individual velocity measurements consisted of the average instantaneous velocity measured
during a 20 second time interval. A number of surface spot velocities were also recorded at
several stations.

Flow calculations were completed using the Velocity-Area Method. This technique involves
dividing a cross-section of the river into a number of segments, each bounded by imaginary
vertical lines from the water surface to the stream bed. The area of each segment is determined
and the mean velocity of water flowing through it is determined from velocity measurements.
The discharge for each segment is computed by multiplying the area of the segment by the
corresponding mean velocity, and these individual discharges are added to obtain the total
discharge.

10

Statistical Analyses

Several methods of data analysis were used to evaluate water and sediment quality, and selected
biotic communities in the study area. Statistical methods were generally selected because of their
recognized utility in delineating spatial and temporal variation, or ability to quantitatively
summarize associations and trends. A brief summary of the rationale and application, and the
mathematical formula for each analysis is presented below.

1) Indices

Indices provide a simple method of summarizing complex data. They are derived variables such
as a ratio of one variable divided by a standard variable. When applied to invertebrate data,
such indices generally involve ratios of numbers of taxa and numbers of individuals in the
collected samples. These indices have interpretive value as data summaries.

i) .Shannon-Weaver (or Shannon-Weiner) Diversity Index (H')

Diversity is a measure of the distribution of observations among categories (e.g. species). When
applied to communities of invertebrates, diversity calculations incorporate counts of organisms
within each taxonomic group. A low diversity is the result of a concentration of invertebrates
in few categories; and conversely, a more uniform distribution of organisms among all categories
results in a high diversity. Diversities greater than 3.0 are indicative of an unpolluted
environment, whereas diversities less than 1.0 indicate severely polluted conditions ( Weed and
Rutschlcy, 1972). The formula for the Shannon-Weaver diversity index, H' is:

N. N.

n -^ n

where n = the total number of individuals in the sample
N , = the number of individuals in the "i"th sample
S = the number of categories (taxa) with known proportional abundance

ii) Brillouin Diversity Index

Brillouin's Diversity H, is "the species diversity per individual of a collection in which all n
specimens have been assigned to one of s species, and counted to give the N,'s" (Kaesler et al. ,
1978). Unlike Shannon's index, it can give the actual diversity of a fully censused collection
of invertebrates. In addition, it is an actual measurement of the diversity of the sample, and is
not just a statistical estimate. The formula used to determine Brillouin's index of diversity is
given below:

H=— (logi2! -^ logN^

where n = the total number of individuals in the sample
N i = the number of individuals in the "i"th sample
S = the number of categories (taxa) with known proportional abundace

2) Cluster Analysis

Benthic invertebrate communities were defined with the use of cluster analysis, which reduces
the species abundance data to a graphical summary. The resultant groups or clusters
characterize relatively homogeneous species assemblages (Green, 1979). The significance of
group separation relative to environmental variables can be evaluated by multiple discriminant
analysis, which is discussed on the following page.

In order to confirm the robust nature of the results, several cluster analysis techniques were
used, including:

i) Minimum Variance Clustering (Ward's Method)
ii) Group Average Clustering
iii) Centroid Clustering

Cluster analysis was completed on abundance data and presence/ absence data with use of'
SYSTAT software (Wilkinson, 1988).

Some problems may be encountered in the use of cluster analysis, including: (i) the subjective
choice of clustering method and similarity measure will affect the outcome; and (ii), clusters
may be produced when they do not exist (Jackson er ai, 1989). The patterns revealed by the
cluster analyses were confirmed with the use of Principal Components Analysis (PCA).

3) Principal Components Analysis

Principal components analysis (PCA) was used to analyze the benthic invertebrate data and to
verify station groupings defined by cluster analysis. PCA is a technique for deriving linear
combinations of the original variables, called principal components, that are orthogonal to one
another, and that successively account for the largest portion of the residual sample variance
(Rogers, 1971). This method, as with most multivariate statistics that reduce the dimensionality
of multivariate observations, is used to generate a smaller number of variables that summarize
most of the information contained in the original variables.

The "factor loadings" produced during principal components analysis are correlation coefficients
between each original variable and each principal component. Since species abundance data
rarely conform with the linearity assumptions associated with the use of correlations and
covariances in PCA (Ludwig and Reynolds, 1988), we chose to use rank correlations in the
PCA's (Rising and Somers, 1989). The data were ranked prior to completing the PCA, and the
first two or three factors were graphed for presentation in this report.

The PCA's were calculated with use of the SYSTAT computer program and were presented
graphically with use of SYGRAPH software (Wilkinson, 1988).

4) Discriminant Analysis

Discriminant analysis was used to evaluate differences among the defined benthic communities
with respect to environmental conditions (sediment parameters). Discriminant analysis is a
multivariate technique used to distinguish groupings (e.g. communities) on the basis of a series
of quantitative descriptors (e.g. sediment chemistry). The resultant discriminant axes (functions)
are linear combinations of the sediment chemical variables that maximize differences between
the groups of communities. Each axis is mterpreted with the use of correlation coefficients (r)
between the discriminant functions and the original sediment parameters.

Eleven sediment variables were used to discriminate between benthic communities (Table 5).
Grain (particle) size data was not available and could not be used in the analysis.

Table 5 : Sediment-quality parameters used in discriminant analysis.

METALS

NUTRIENTS

OTHERS

Zinc

Loss on Ignition

Oil and Grease

Cadmium

pH

Copper

Lead

Chromium

Aluminum

Mercury

Arsenic

All variables were logarithmically transformed prior to use in discriminant analysis.
Concentrations below detection limits were set equal to the detection limit.

Discriminant analysis was completed on the benthic communities defined by cluster analysis, as
well as on individual sampling stations. Discriminant analysis was conducted using SYSTAT
computer software. Double precision was used during the analysis, as discriminant analysis is
particulariy sensitive to rounding errors (Green, 1979).

Results and Discussion

Water Quality

Water quality was evaluated at a total of 25 sites on the Welland River (Appendix I and
Appendix XI). Water quality varied among stations, with concentrations of several parameters
(including iron, copper and mercury) exceeding Provincial Water Quality Objectives (PWQO's)
at some stations. Several water-quality parameters were below detection limits. A list of metals
and other parameters which were below detection limits is presented in Table 6.

Table 6: Water-quality parameters below detection limits in all the Welland River water
samples.

Chemical

Parameter

Symbol

Detection Limit

Cadmium

Cd

0.002 mg/L

Cobalt

Co

0.005 mg/L

Lead

Pb

0.01 mg/L

Chromium

Cr

0.005 mg/L

Nickel

Ni

0.005 mg/L

Beryllium

Be

0.005 mg/L

Molybdenum

Mo

0.005 mg/L

Vanadium

V

0.005 mg/L

Arsenic

As

0.005 mg/L

Antimony

Sb

0.002 mg/L

Selenium

Se

0.001 mg/L

Silver

Ag

0.005 mg/L

Phenolics

0.001 mg/L

Total Cyanide

CN

0.002 mg/L

Following is a summary of the water-quality results. Concentrations of water-quality parameters
are illustrated in Appendix I. ^

Iron

Iron concentrations exceeded the PWQO at stations 1, 15, and 21 (Appendix I); and levels of
iron ranged from a low of 0.06 mg/L at station 23 to a high of 2.1 mg/L at station 1. Iron
levels reported by Hart (1986) near the Queenston-Chippawa Power Canal ranged from 0.420
mg/L to 0.840 mg/L respectively. A study by Johnson (1964) throughout the river noted levels
between 0.62 mg/L and 6.16 mg/L.

Copper

During the summer survey, copper levels exceeded the PWQO at all stations with the exception
of stations 3, 10a, 15, 19a, and 23. Levels of copper were reduced during the fall survey;
however stations 2, 4, 10, 15, and 23 exceeded the PWQO. Copper concentrations ranged from
below detection limits to 0.05 mg/L. Concentrations reported by Hart (1986) were within this
range.

Mercury

Mercury concentrations ranged from a low of <0.05 fxg/l at most stations to a high of 0.30 /xg/1
at station 1 (Appendix 1). Mercury levels exceeded the PWQO at stations 1,2, and 3 during
the summer survey; however all the stations had concentrations below detection during the fall
survey.

The high concentrations of mercury in water samples from stations 1 - 3 may be due to the
bacterial methylation of mercury in an upstream reservoir (Lake Niapenco). Mercury levels may
have been lower during the fall survey because of lower water temperatures which reduce the
metabolic activity of bacteria. Mercury concentrations reported by Hart (1986) near the
Queenston-Chippewa Power Canal ranged from below detection to 0.02 mg/L.

Aluminum. Magnesium, and Zinc

Aluminum levels ranged from a low of 0.09 mg/L at station 9 to a high of 3.4 mg/L at station
3, and concentrations were found to be higher in those water samples taken during the fall
survey. The MOE guideline for total aluminum in clay-free samples is 0.075 mg/L. All
stations exceeded this guideline. Elevated aluminum concentrations may be due to the high
suspended clay content in the water column rather than the influence of any specific contaminant
sources.

Magnesium concentrations at the "extensive" stations were between 8.4 mg/L and 14.1 mg/L
(Appendix I). There is currently no PWQO for this parameter in water.

16

Zinc levels were below detection limits in all water samples except those from stations 1 and 24
(Appendix I). Concentrations noted at stations 1 and 24 were below the PWQO. Zinc
concentrations reported by Hart (1986) ranged between 0.005 mg/L and 0.01 mg/L, and were
all below the PWQO.

Long Term Monitoring

Water quality has also been monitored on an ongoing basis by MOE at a number of sites on the
Welland River, including the Montrose Bridge (station 21). Temporal trends of zinc, copper,
chromium, mercury, and lead concentrations at the Montrose Bridge between 1979 and 1987 are
illustrated in Figure 3. There is generally a reduction over time in levels of these metals in the
Welland River water at this site.

The Ministry has also monitored aluminum levels at the Montrose Bridge and at a site near Port
Robinson (Figure 4). There appears to be a slight increase in mean aluminum concentrations
between 1981 and 1987, with the highest levels noted during 1985 at both stations. As discussed
on the previous page, the high aluminum concentrations may be due to high levels of suspended
clay in the water, rather than a specific contaminant source.

Phosphorus

Total Phosphorus (TP) at the 25 stations ranged from 0.013 mg/L to 0.25 mg/L (Appendix I).
The PWQO for TP was exceeded at all stations except for stations 9, 10, 22, 23, and I9a. Low
levels of TP were found at stations 22 and 23, which receive water from the Niagara River that
is diverted to the Queenston-Chippewa Power Canal. Water samples from stations 1 through
6, had high levels of TP, probably due to the influence of agricultural activities in and above
section A.

Total phosphorus data during the period 1979 to 1987 at the MOE water quality stations are
illustrated in Figure 5. The concentration of total phosphorus in the water varied among years;
however, the Welland Airport station had consistently higher levels of total phosphorus than
those found-at the downstream stations. This pattern was most likely due to dilution of water
in the lower reaches of the river from the Welland Ship Canal, and to assimilation of phosphorus
by biota.

17

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Total Kieldahl Nitrogen

Total Kjeldahl Nitrogen (TKN) levels during the August 1990 survey ranged from 0.28 mg/L
to 2.6 mg/L (Appendix I). As with TP, higher levels of TKN were found at sampling stations
located in section A, most probably due to the influence of agricultural activities. The highest
level of TKN was noted at station 21 located below the Montrose Bridge.

Mean yearly TKN levels for the period 1979 to 1987 at MOE water quality stations are
presented in Figure 6. TKN levels at MOE stations located at the Welland River Airport and
at Port Robinson have remained fairly constant over the years, whereas TKN levels at the
Montrose Bridge station have decreased dramatically. The decrease in TKN at the Montrose
Bridge is most likely due to improvements in effluent quality from Cyanamid. The main
nitrogen treatment system became operational in 1985.

Ammonia concentrations ranged from 0.008 to 0.333 mg/L, and levels of nitrite and nitrate
ranged from 0.003 to 0.04 mg/L and 0.16 to 0.56 mg/L, respectively. Station 21, at the
Montrose bridge, had the highest levels of these parameters due to the discharge of nitrogen
species from Cyanamid to Thompson's Creek.

PAHs. PCBs. and PC Pesticides

All PAHs, OC pesticides and PCBs were below detection limits (Tables 7 and 8 respectively).
The Ministry of the Environment has also monitored OC pesticide levels from 1981 to 1989
(MOE-unpublished data (1981-1989)). Most pesticides were below detection limits; however
alpha-BHC and gamma-BHC were detected in trace quantities for all years. Endosulfan sulfate,
beta-BHC, 4,4'-DDE, and 4,4'-DDT were also detected in trace amounts for some years.

Organic compounds ifrom sites 6 and 21, which were analyzed at the MOE laboratory, were also
below detection limits (Table 8b).

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Table 7: Polycyclic aromatic hydrocarbons and associated detection limits

PAH Detection Limit (/xg/L)

Naphthalene

0.1

Acenaphthylene

0.1

Acenaphthene

0.1

Fluorene

0.1

Phenanthrene

0.2

Anthracene

0.2

Fluoranthene

0.2

Pyrene

0.2

Benzo(a)anthracene

0.2

Chrysene

0.2

Benzo(b)fluoranthene

0.5

Benzo(k)fluoranthene

0.5

Benzo(a)pyrene

0.5

Perylene

0.5

Indeno(l,2,3-c,d)pyrene

2

Dibenzo(a,h)anthracene

5

Benzo(g,h,i)peryIene

1

23

Table 8: Organochlorine pesticides and associated detection limits

OC Pesticide Detection Limit (/xg/L)

Hexachlorobenzene

0.003

alpha-BHC

0.003

gamma-BHC

0.003

Heptachlor

0.003

Aldnn

0.003

beta-BHC

0.003

Oxychlordane

0.003

Heptachlor epoxide

0.003

Endosulfan I

0.003

gamma-Chlordane

0.003

alpha-Chlordane

0.003

4,4'- DDE

0.003

Dieldrin

0.003

Endrin

0.003

2,4'- DDT

0.003

4,4'- DDD

0.003

Endosulfan II

0.003

4,4'-DDT

0.003

Mirex

0.003

Endosulfan Sulfate

0.005

Methoxychlor

0.005

PCB's (Total)

0.050

24

Parameter

D. L.

(ng/L)

6 21

Extractable Org.

N.A.

no numeric result

Volatile Org.

N.A.

no numeric result

Octachlorostyrene

N.A.

no suitable sample

PCB, Total

20

below detection limit

Hexachlorobenzene

1

below detection limit

Heptachlor

1

below detection limit

Aldrin

1

below detection limit

PP-DDE

1

below detection limit

Mirex

5

below detection limit

A-BHC Hexachlorocyclohex

1

below detection limit

B-BHC Hexachlorocyclohex

1

below detection limit

G-BHC Hexachlorocyclohex

1

below detection limit

A-Chlordane

2

below detection limit

G-Chlordane

2

below detection limit

Oxychlordane

2

below detection limit

OP-DDT

5

below detection limit

PP-DDD

5

below detection limit

PP-DDT

5

below detection limit

DMDT Methoxychlor

5

below detection limit

Heptachlorepoxide

2

below detection limit ■

Endosulfan I

2

below detection limit

Dieldrin.

• 4

below detection limit

Endrin

4

below detection limit

Endosulfan II

4

below detection limit

Endosulfan Sulphate

4

below detection limit

D.L. is detection limit. N.A. means no numeric value was reported.

25

Water temperature, conductivity, and dissolved oxygen as determined in the field are presented
in Appendix III. All values are within ranges considered normal.

A comparison of the water quality in the study area of the Welland River with several of its
tributaries and the Niagara River is presented in Table 9. Water quality of the Welland River
is generally similar to that of Thompson's Creek, Lyons Creek, and the Niagara River, with the
exceptions of TKN and total phosphorus. Concentrations of these parameters are higher in
Thompson's Creek than in the lower Welland River, probably because of the influence of
Cyanamid. Levels of iron and aluminum are also slightly elevated in the lower Welland River
compared with concentrations in the other river systems. This phenomenon is probably due to
the influence of metal industries located on the Welland River, and the high suspended cay load
in the water column.

26

Table 9: Comparison of water quality of the Welland River with selected river systems in the
area. All parameters are in mg/L unless otherwise specified.

Parameter

Welland
River

Thompson's
Creek'

Lyon's
Creek'

Niagara
River ^

Fe

0.06-2.1

0.510-0.720

0.120-1.20

ND-0.3.2

Al

0.09-3.4

0.370-0.440

0.110-0.950

ND-2.6

Ni

ND

0.007-0.016

0.002-0.004

ND-0.04

Zn

ND-0.02

0.020-0.030

0.004-0.036

ND-0.03

Cu

ND-0.04

0.020-0.032

0.003-0.019

ND-0.029

Cr

ND

0.005-0.054

ND-0.002

ND-0.260

Pb

ND

ND-0.006

ND-0.011

ND-0.005

Cn

ND

NA

NA

ND

Cd

ND

0.0002-0.0003

ND-0.0005

ND-0.0004

Hg

ND-0.0003

0.040-0.050

ND-0.010

ND-0.0006

As

ND

0.001

ND

ND-0.003

TP

0.013-0.149

0.60-1.26

0.015-0.039

NA

TKN

0.28-2.6

97.5-485

0.020-0.310

NA

ND - not detected
NA - not analyzed

1 - Hart (1986)

2 - Kauss (1983); from stations in the Lower River, the Tonawanda Channel, and the Chippawa
Channel.

Sediment Quality

Sediment quality was extremely variable throughout the study area (Appendices II and XII).
When compared with the Draft Provincial Sediment Quality Guidelines (PSQG) and in some
cases the existing Open Water Disposal Guidelines (OWDG), concentrations of a number of
metals, nutrients, and oil and grease exceeded the criteria at several stations.

The OWDG's (Persaud and Wilkins, 1976) were originally intended for use in assessing the
suitability of soils and dredged material proposed for open-water disposal. Until recently, these
guidelines have also been used to evaluate contaminant levels in existing aquatic sediments. The
Draft PSQGs (Persaud ei ai, 1990) are recently developed guidelines which are specifically

27

intended to protect aquatic biological resources. These guidelines are based on three levels of
ecotoxic effects: a no-effect level (NOEL), a lowest effect level (LEL), and a severe effect level
(SEL) (Table 10).

Table 10: Provincial Sediment Quality Guideline levels and their significance (Persaud et al,
1990 - Draft)

Guideline Level

Sediment Quality

Potential Impact

> SEL

Grossly Polluted

Will significantly impair use of
sediment by benthic organisms

< SEL
> LEL

Significantly Polluted

Will impair sediment use by some
benthic organisms

< LEL
> NOEL

Clean - Marginally Polluted Potential to impair some sensitive water
uses

< NOEL

Clean

No Impact on water quality, water uses,
or benthic organisms anticipated

Lead

Lead levels in sediments exceeded the PSQG-LEL of 3 1 ^g/g at all stations during the summer
survey, except for stations 2, 4, 11, 13, 14, 15, 16, 19a, 21, 22, and 23 (Appendix II).
Stations 13 and 14 were the only stations having sediment lead levels below the LEL during the
fall survey. The highest lead concentrations were found at stations 9 and 12 (138 /ig/g and 91
^g/g, respectively) during the fall survey, whereas stations 22 and 23 had the lowest levels
during the summer survey.

All sediment samples had lead levels less than the SEL of 250 /xg/g.

28

Chromium

Chromium concentrations exceeded the PSQG-LEL of 26 ^g/g at most stations (95%) with the
exception of stations 22 and 23 located in Chippawa Creek (Appendix II). Extremely high
chromium levels were noted in sediments collected from stations 10, 12, and 17 during both the
summer and fall surveys. Chromium concentrations in sediments at stations 10 and 12 were
approximately 26 and 18 times the LEL, respectively.

The SEL of 1 10 /^g/g was only exceeded at stations located in sections B and C of the study
area. Sediments from stations 12, 13, 15, 17, and 18 during the summer survey, and stations
10, 10a, 11, 12, 13, 14, 15, 16, 17, 18, and 19 during the fall survey were characterized by
chromium concentrations in excess of the SEL.

Sediment mercury levels exceeded PSQG-LEL of 0.2 yug/g at stations 8, 9, 10a, 12, 16, 18, and
19 during the summer survey, and at stations 7, 8, 9, 10, 11, and 12 during the fall survey
(Appendix II). Sediments collected from station 9 had the highest mercury concentrations during
both surveys (approximately 16 and 21 times the LEL).

The SEL of 2 ;ag/g was only exceeded at station 9 during both the summer and fall surveys.

Cadmium

Cadmium levels were extremely variable throughout the study area, and exceeded the PSQG-
LEL of 0.6 /ig/g at stations 9, 10, 12, 19, and 22 during the summer survey, and at stations 7,
9, 10, 10a, 11, 12, 17, and 19 during the fall survey (Appendix 11).- Station 12 was
characterized by the highest cadmium levels during both the summer and fall surveys (1.4 /xg/g
and 1.5 /xg/g, respectively).

All sediment samples had cadmium levels well below the SEL of 10 pLg/g.

Arsenic

Arsenic levels exceeded the PSQG-LEL of 6 fxg/g at stations 3, 9, 10, 10a, 12, 18, 19, and 20
during the summer survey and at stations 10, 12, 14, 15, 17, 19, 19a, and 20 during the fall
survey (Appendix II). The highest concentrations were found in sediments at stations 10 and
12, and the lowest levels were found at stations 22 and 23.

All sediment samples had arsenic levels below the SEL of 33 /xg/g.

29

Zinc

Zinc concentrations exceeded the PSQG-LEL of 120 ^J.glg at stations 7, 9, 10, 10a, 12, 17, 18,
19, and 19a during the summer survey, and at stations 5, 7, 8, 9, 10, 10a, 11, 12, 14, 15, 16,
17, 18, 19, 19a, and 20 during the fall survey (Appendix II). Sediments collected from stations
10 and 12 had the highest zinc levels; 555 /^g/g and 620 /xg/g respectively.

The SEL of 820 /^g/g was not exceeded at any of the stations.

Iron

All sediment samples collected in the study area exceeded the PSQG-LEL of 20 mg/g (2%) for
Iron, with the exception of station 23 during the summer survey (Appendix II). Of the five
"extensive" stations evaluated during the summer survey, only station 15 had iron levels
exceeding the SEL of 40 mg/g (4%).

Iron levels in excess of the SEL were found at stations 10, 10a, II, 12, 13, 14, 15, 16, 17, 18,
19, and 20 during the fall survey, with the highest concentration from station 10 (118 mg/g).

Nickel

The PSQG-LEL of 16 /xg/g for nickel was exceeded at the five "extensive" stations sampled in
the summer, and at all the stations evaluated m the fall. Nickel concentrations ranged from
highs of 390 ixgig and 270 p.glg at stations 10 and 12 respectively to a low of 19.5 /xg/g at
station 23 (Appendix II).

The SEL of 75 ^g/g was exceeded at station 15 during the summer survey, and at all stations
in sections B and C (with the exception of station 9) during the fall survey.

Copper

Most sediment samples had copper levels in excess of the PSQG-LEL of 16 /xg/g, with the
exception of stations 22 and 23 during the summer survey (Appendix II).

The SEL of 1 10 /xg/g was exceeded at station 19 during the summer survey, and at stations 10,
19, 19a, and 20 during the fall survey. The highest copper concentrations were noted at station
10 and station 20.

30

Other Metals

Concentrations of several other metals were also evaluated during the summer survey, including
aluminum and magnesium (Appendix II). Aluminum concentrations varied a great deal
throughout the study area with the highest levels occurring stations 3, 12, and 19. Stations 22
and 23 had the lowest aluminum concentrations.

Magnesium levels were evaluated at the five "extensive" stations, and ranged from alow of 9.9
mg/g at station 1 to a high of 17.2 mg/g at station 23.

Nutrients

Loss on ignition (LOI) was measured at all the stations in the study area, whereas total kjeldahl
nitrogen (TKN), total phosphorus (TP), and total organic carbon (TOC) were evaluated at all
the "extensive" stations during the summer survey.

LOI is a measure of the particulate organic matter (leaves, bark, sewage, fibres) in the sediment.
LOI for sediments ranged from a low of 2 percent at stations 11, 13, 14, and 15, to a high of
14 percent at station 1 (Appendix II). Sediment samples collected from section A of the river
were also characterized by higher LOI levels.

Total kjeldahl nitrogen levels exceeded the PSQG-LEL of 550 /xg/g at stations 1, 9, 21, and 23
(Appendix II). Concentrations ranged from a low of 290 /xg/g at station 15 to a high of 2800
/Lig/g at station 1. All sediment samples had TKN levels below the SEL of 4,800 jxglg.
Similarly, TOC values exceeded the PSQG-LEL of 1 percent at stations 1, 9, 21, and 23
(Appendix II). TOC levels ranged from a low of 0.92 percent at station 15 to a high of 7.4 at
station 1. The SEL of 10 percent was not exceeded at any station.

Total phosphorus concentrations exceeded the PSQG of 600 /xg/g at all stations, and ranged from
620 ixgig at station 23 to 1300 /xg/g at station 21 (Appendix II). All sediment samples had TP
levels below the SEL of 2000 /xg/g.

Total Cyanide

Total cyanide was determined at all stations during the summer stirvey and at a subset in the fall.
Concentrations were below detection limits in most instances (Appendix II). The OWDG of O.I
/xg/g (no existing PSQG) was exceeded at station 1 and station 20 during the summer survey,
and at stations 2, 17, 18, 19a, 20, and 21 during the fall survey. Sediments collected from
station 20 had the highest cyanide level of 1.67 /xg/g,

Oil and Grease

Concentrations of oil and grease ranged from a low of 195 /xg/g at station 13 to a high of 1 1 ,800
/xg/g at station 12 (Appendix II). Oil and grease levels exceeded the OWDG of 1,500 jxg/g (no
existing PSQG) at a number of stations during both the summer and fall surveys, predominantly
in the urban area of the City of Welland and the industrial section east of Port Robinson.

Polycyclic Aromatic Hydrocarbons

The polycyclic aromatic hydrocarbon (PAH) analytical results for all sediment samples collected
in the summer and fail are presented in Table 1 1 and 12 respectively. Station 9, in downtown
Welland, had extremely high levels of all the PAHs relative to those found at other stations
during the summer and fall surveys. Station 10, located near the McMaster Avenue outfall,
also had high levels of some PAHs during the fall survey.

Total PAH levels at stations 1 and 9 exceeded the PSQG-LEL of 2,000 ng/g during the summer
survey. SEL levels were not exceeded at any of the stations tested during the summer survey.
Total PAHs exceeded the PSQG-LEL at stations 7, 8, 9, 10, and 15 during the fall survey.
SELs for organic compounds are dependent on the amount of organic carbon in the sediment
(MOE 1991). SELs could not be calculated for the fall survey because TOC concentrations
were not measured.

PAH concentrations were extremely variable, both between surveys, and between duplicate
samples collected from the same station. This phenomenon probably reflects the uneven
distribution of the contaminants within the sediments.

Polychlorinated Biphenyls

Polychlorinated biphenyls (PCBs) were not detected in any sediment samples collected during
the summer survey; however they were detected in several fall samples. Total PCB levels
ranged from <0.05 ^g/g to 0.13 /xg/g, and exceeded the PSQG-LEL of 0.07 /xg/g at stations
7, 8, 9, and 15 (Appendix IÏ). The SEL could not be calculated as TOC levels were unavailable
for the fall survey.

Results from detailed chemical analyses conducted by MOE on sediments from stations 6, 9, 15
and 21 indicated total PCB concentrations at station 21 also exceeded the LEL (Table 12b). The
laboratory report noted that PCB congeners detected at site 21 resembled a mixture of Aroclor
1254 and 1260. PCBs were not detected at the other stations 6, 9 or 15.

32

Table 1 1 : Concentrations of PAHs in Welland River sediments collected during the summer
survey. All concentrations are in ng/g.

1 PAH

Stn 1

Stn 9 *

Stn 15

Stn 21

Stn 23

Naphthalene

22

129 (290)

19

<10

16

Acenaphthylene

<10

<10(15)

<10

<10

<10

Acenaphthene

13

200 (880)

<10

<10

<10

Fluorene

33

270 (710)

<10

<10

12

Phenanthrene

200

1630 (4100)

24

52

63

Anthracene

95

490 (1590)

14

25

55

Fluoranthene

400

2100(7200)

82

210

210

Pyrene

370

2200 (7200)

104

240

210

Benzo(a)anthracene

125

1050 (4000)

30

79

126

Chrysene

148

1020 (3700)

35

101

175

Benzo(b)flouranthene

260

1600 (5700)

90

220

300

Benzo(k)flouranthene

260

1600(1900)

90

220

116

Benzo(a)pyrene

69

1470 (5400)

61

140

170

Perylene

680

570 (1490)

31

97

101

Indeno(123,cd)pyrene

<100

1150(5200)

<100

83

<100

Dibenzo(ah)anthracene

<100

1390 (4800)

<100

<100

<100

Benzo(ghi)perylene

<50

470(1500)

<50

35

<50

Total PAH's'

2 '125

16774
(54185)

689

1475

1487

1 - Total PAHs is the sum of all the PAHs listed except for perylene. Concentrations of PAHs
below detection limits were taken as equal to half the detection limit.

* - Value in brackets is the PAH concentration in a duplicate sample taken from the three ponar
samples taken at each station

33

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Table 12 b: MOE results for concentrations of chlorinated organics at sites 6, 9, 15 and 21.

Parameter

Units

D.L.

Station

21

T4CDD

P5CDD

H6CDD

H7CDD

08CDD

T4CDF

P5CDF

H6CDF

H7CDF

08CDF

Ex tractable Org.

Volatile Org.

PCB, Total

Hexachlorobenzene

Heptachlor

Aldrin

Mirex

a-BHC

/3-BHC

7-BHC

A-Chlordane

G-Chlordane

Oxychlordane

PP-DDE

OP-DDT

ppt

*

ppt

*

ppt

N.A

ppt

N.A,

ppt

N.A,

ppt

*

ppt

*

ppt

N.A,

ppt

N.A.

ppt

N.A,

N.A.

N.A.

N.A.

N.A.

ng/g

20

ng/g

1

ng/g

1

ng/g

1

ng/g

5

ng/g

1

ng/g

• 1

ng/g

1

ng/g

2

ng/g

2

ng/g

2

ng/g

1

ng/g

5

ND

ND(4)

ND(7)

ND(6)

ND(7)

ND(12)

ND(9)

793

31^

60^

230^

,230^

420^

1900'

2300'

3100'

ND(5)

ND(8)

ND(7)

14>

ND(12)

ND(7)

30^

12'

28^

160-

922

140'

63'

36'

81'

2(T)

no numeric result
no numeric result
ND ND

below detection limit
below detection limit
below detection limit
below detection limit
below detection limit
below detection limit
below detection limit
below detection limit
below detection limit
below detection limit

2(T) ND

below detection limit

85 (T)

4(T)

35

Table 12 b: Continued

Parameter

Units

D.L.

Station

6 9 15 21

PP-DDD

ng/g

5

below detection limit

PP-DDT

ng/g

5

below detection limit

DMDT Methoxychlor

ng/g

5

below detection limit

Heptachlorepoxide

ng/g

1

below detection limit

Dieldrin

ng/g

2

below detection limit

Endrin

ng/g

4

below detection limit

Endosulfan I

ng/g

2

below detection limit

Endosulfan II

ng/g

4

below detection limit

Endosulfan Sulphate

ng/g

4

below detection limit

Octachlorostyrene

ng/g

1

below detection limit

D.L. is the parameter detection limit.

Asterisks (*) indicate parameter detection limits may be found in brackets ( ) for each station.

N.A. indicates a numeric value or result was not reported.

A superscript denotes the number of isomers of that parameter detected at that station.

ND indicates that parameter exists at a concentration below D.L. at that station.

(T) means the parameter was measured in trace amounts at that station. Interpret with caution.

36

Pesticides

Organochlorine (OC) pesticides were not detected at any of the sampling stations. A list of all
OC pesticides and their detection limits is presented in Table 13. The Ministry of the
Environment has also routinely determined OC pesticides in Welland River sediments from 1981
to 1988 (MOE-unpublished' data (1981-1988)). Alpha-BHC, alpha-chlordane, dieldrin,
hexachlorobenzene, 4,4'DDE and gamma-chlordane were detected in some years.
Concentrations were consistently low. With the exception of PP-DDE, which was detected in
trace amounts at stations 6, 9 and 21, pesticides analyzed by MOE for the preSent study were
below detection limits (Table 12b).

Dioxins and Furans

Polychlorinated dibenzo-p-dioxins were found at stations 9, 15, and 21 (Table 12b).
Concentrations ranged between 31 and 79 ppt for hexachlorinated forms, 230 to 420 for the
heptachlorinated forms, and 1,900 and 3, 100 for the octachlorinated congener. Polychlorinated
dibenzofurans were also detected at the same stations. A pentachlorinated congener was found
only at station 9 and at a concentration of 14 ppt. The hexa, hepta, and octachlorinated forms
were found at stations 9, 15, and 21 at levels ranging from 12 to 30, 92 to 160, and 36 to 81
ppt respectively.

The more highly chlorinated dioxin and furan congeners such as the octachlorinated forms are
generally believed to be less of an environmental concern than are the tetrachlorinated isomers
because of the relatively large size of the molecules. The larger molecules tend to bind tightly
to sediment particles and have a high octanol-water partition coefficient; and because of the large
size, they cannot cross cell membranes easily. The toxicity of these contaminants to aquatic
biota is poorly understood at present; however, it is acknowledged that they can affect growth,
reproduction, and hormonal processes in some organisms.

37

Table 13 : Organochlorine pesticides, PCBs and associated detection limits in

sediments.

OC Pesticide Detection Limit (/xg/g)

Hexachlorobenzene

0.003

alpha-BHC

0.003

gamma-BHC

0.003

Heptachlor

0.003

Aldrin

0.003

beta-BHC

0.003

Oxychlordane

0.003

Heptachlor epoxide

0.003

Endosulfan I

0.003 .

gamma-Chlordane

0.003

alpha-Chlordane

0.003

4,4'- DDE

0.003

Dieldrin

0.003

Endrin

0.003

2,4'- DDT

0.003

4,4'- DDD

0.003

Endosulfan II

0.003

4,4'-DT

0.003

Mi rex

0.003

Endosulfan Sulfate

0.003

Methoxychlor

0.003 - 0.005

PCBs

0.050-0.100

38

Sediment Contamination by Station

Sediment quality in the study area with respect to the PSQGs for metals, and OWDGs for oil
and grease and total cyanide, is summarized in Table 14.

Sediments at stations 9, 10, 10a, 11, and 12, located in the upstream portion of section B, along
with those at stations 15, 16, 17, 18, 19 and 20 in section C are the most contaminated, as
indicated by the levels of several metals and oil and grease. Concentrations of chromium,
mercury, iron, nickel, and copper also exceed the SEL's at several stations in sections B and C.

Station 7, which also has relatively contaminated sediments, is located in the eastern downstream
portion of section A below a large storm sewer. Storm water is a known source of heavy metals
and oil- and grease. Inputs to this storm drain may be the cause of contaminants accumulating
in sediments at this site.

Sediments at station 9 are characterized by high concentrations of metals, oil and grease and a
number of PAHs. A large storm drain located upstream of this station is the suspected source
of contaminants. Elevated levels of several metals have also been found in sediments at this
location during previous studies (Acres 1990). A comparison of results from the Tarandus and
Acres studies is presented in Table 15. Concentrations are also compared with PSQG lowest
effect and severe effect levels.

Sediments at stations 10 and 10a, situated a short distance downstream from the Atlas Steel
outfall and downstream from the old McMaster Avenue combined sewer outfall also have
elevated levels of several metals, and oil and grease. A reef-type deposit of industrial waste was
first noted off the Atlas outfall by Brindle and Dickman in 1980 (Acres, 1990). Acres (1990)
examined this deposit in detail and also discovered two areas of further contamination, one at
the outfall from the McMaster Avenue combined sewer, and one approximately 400 meters
downstream from the Atlas outfall. The reef sediments contained elevated levels of copper,
chromium, iron, lead, manganese, nickel, zinc, and oil and grease. A comparison of sediment
quality results from the 1990 Tarandus survey and the Acres study is presented in Table 16.

The discharge outfall from Atlas Steel has been well documented as a source of contaminants
to the Welland River (COA, 1981; NRTC, 1984). The industrial effluent was also documented
as exceeding effluent guidelines for several parameters including chromium, copper, lead,
nickel, zinc, iron, phosphorus, nitrogen, and sulphate (NRTC, 1984; Dalrymple in Dickman and
Hayes, 1985).

39

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Table 15: A comparison of selected sediment-quality parameters at station 9. All results are
in Mg/g-

Parameter

Tarandus (1990)

Acres (1990)

PSQG
LEL

PSQG
SEL

Chromium

50.0-320.0

14.0-79.0

26

110

Copper

79.0-126.0

33.0-146.0

16

110

Lead

49.0-138.0

24.0-339.0

31

250

Manganese

400.0-750.0

269.0-794.0

460

1100

Nickel

37.0-195.0

25.0-140.0

16

75

1 Zinc

158.0-460.0

242.0-2236.0

120

820

Table 16: Comparison of selected parameters in sediments collected offshore of the Atlas
outfall. All results are in>g/g.

Parameter

Tarandus (1990)'

Acres (1990)'

Chromium

91.0-670.0

21.0-5,000

Copper

50.0-168.0

17.0-860.0

Iron

11,800

20,000-420,000 1

Lead

38.0-87.0

15.0-870.0

Manganese

1,210

470.0-6,600

Nickel

390

37.0-11,000

Zinc

270.0-550.0

36.0-690.0

PCBs

< 0.05-0.045

< 0.2-0.3^

1 - sediment quality results for stations 10 and 10a

2 - sediment quality results for 18 samples taken from an area 20 meters upstream and 20

meters downstream of the Atlas outfall

3 - PCBs analyzed at 3 stations directly off the outfall

Sediments at station 11, located downstream from the Welland Water Pollution Control Plant
(WPCP) also exceed PSQG-LELs for several metals, and oil and grease. These sediments also
exceeded SEL's for chromium, iron, and nickel. The WPCP effluent has also been documented
as exceeding effluent guidelines for copper, lead and zinc (NRTC, 1984).

Solid waste (primarily slag) and liquid waste from Atlas Steel (primarily slag) has been deposited
since 1930 at the company's landfill located on the east bank of the river and has in the past
been documented as a source of contaminants to the Welland River through surface runoff
(NRTC, 1984). Contaminants include aluminum, arsenic, cadmium, chromium, copper,
mercury, nickel, lead, selenium, zinc, and cyanide.

All stations located in section C were also characterized by elevated levels of several metals,
total cyanide, and oil and grease. The Cyanamid Canada plant located along this section of the
Lower Welland River is considered a source of several contaminants found in the river
sediments. Cyanamid formerly discharged at a point just upstream of station 18, but now
discharges to Thompson's Creek. Thompson's Creek enters the Welland River slightly upstream
of station 20. Cyanamid' s discharge has been reported as a source of several contaminants
including chromium, nickel, zinc, copper, and cyanide (NRTC, 1984). Hart (1986) also
reported elevated sediment concentrations of silver, chromium, mercury, nickel, lead, zinc, and
iron at the mouth of Thompson's creek.

A comparison of selected sediment contaminant concentrations found in several nearby river
systems in the area is presented in Table 17. Means and ranges for the Welland River were
calculated using data for all sites except sites 22 and 23, which are in Chippawa Creek. Mean
sediment concentrations of lead, chromium, mercury, cadmium, arsenic, zinc, nickel and copper
in the Welland River were higher than levels in sediments collected from the Upper Niagara
River or, with the exception of cadmium, from Lyon's Creek. Niagara River sediments had
higher PCB concentrations than Welland River sediments. Elevated levels of several
contaminants in the sediments from Thompson's Creek may be the result of discharges from
industrial processes. The Cyanamid effluent has been reported to be approximately 90 percent
of the average annual flow in Thompson's Creek.

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Benthic Invertebrates

i) Species Composition. Abundance, and Diversity

In total, 90 benthic invertebrate taxa were identified at the 25 sampling stations in the study area
(Appendix IV). The total number of taxa was higher than the number of genera (28) Johnson
in 1964. As might be expected because of the range of habitat types and environmental quality,
the number of taxa at each station varied. It ranged from a low of 12 taxa at stations 6 and 25
to a high of 29 taxa at station 10 (Table 18). The abundance of taxa at stations 9 and 10 may
reflect the diversion of relatively cleaner water from the Welland Canal at the inverted syphon.
The distribution of the various invertebrate species, by number/sample and number/m^ for each
station are presented in Appendix V and VI respectively.

Only two invertebrate species were common to all the sampling stations; Procladius sp. and
immature tubificids, although Chrypiochironomus sp., Limnodrilus hoffineisreri, and Sphaerium
sp. were found at 24 of the 25 sites. Similarly, Johnson (1964) found that Procladius and
Limnodrilus were common throughout the Welland River system.

Tubificids have been used extensively as indicator organisms (Lauritsen ei ai, 1985; Cook and
Johnson, 1974). Limnodrilus hoffineisreri, for example, is a species known to be characteristic
of organically enriched sediments and is generally tolerant of high concentrations of some heavy
metals (Winner et al. 1980). It should be noted, however, that Limnodrilus spp. are not
necessarily confined to polluted waters (Hynes, 1971; Brinkhurst and Cook, 1974). The
abundance of several tubificids, including L. hoffineisreri at all the sampling sites is illustrated
in Figure 7. Relatively high numbers of this species were found at station 9 and station 16.

The chironomids, Procladius sp. and Chironomus sp. are usually common in polluted conditions
(Cook and Johnson, 1974). The relative abundances of Chironomus chironomus and Procladius
sp, at all sampling sites in the study area are illustrated in Figure 8. High numbers of
Chironomus sp. were found at station 9. High abundances of Procladius sp. were found at
stations 10, 11, 15, and 22.

Mayflies, such as Hexagenia sp. are considered intolerant of polluted conditions (Schloesser,
1988; Fremling, 1964; Winner er al., 1980), and as a result, their presence is usually indicative
of uncontaminated conditions. Mayflies were relatively abundant in Section A (stations 1-8),
but were generally absent from the rest of the study area (Figure 9). Johnson (1964) also noted
an absence of mayflies from the same sections of the Welland River.

44

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Zebra mussels {Dreissena polymorpha) are a recent addition to the benthic community in the
study area. Adult Zebra mussels were noted at several stations in sections B, C, and D, most
likely the result of veligers introduced to the Welland River from the Welland Canal at the upper
syphon by the diversion structures. The mussel was not found in section A, probably because
of its inability to move upstream into this section of the river. Zebra mussels found in sections
B, C, and D were attached to rocks and other solid debris as well as to aquatic macrophytes.
Station 9 had the highest density of zebra mussels (1013/m^).

The total abundance of benthic invertebrates ranged from a low of 634 individuals per square
meter at station 12 to a high of 5900 individuals per square meter at station 22 (Table 18).
Station 9 also had a relatively high mean total abundance of 4013 invertebrates per square metre.
Generally, stations located in sections B, C, and D had higher total abundances than those found
in section A, primarily due to higher densities of oligochaetes. Johnson (1964) observed total
invertebrate densities between 97/m^ and 3,757/m^ and also noted higher densities in the eastern
sections of the Welland River.

Figure 10 illustrates the total Oligochaete abundances throughout the study area. The reduction
in the density of oligochaetes at stations below the Atlas Steel discharge and Cyanamid Canada
may be due to the toxicity of the high metal concentrations in these sediments.

The Shannon-Weaver and Brillouin diversity indices for all stations are presented in Table 18.
Benthic-invertebrate diversity fluctuated a great deal, especially in sections B, C, and D.
Diversities at all the stations in section A, were relatively constant. Shannon-Weaver diversities
ranged from a high of 3.96 at station 1 1 to a low of 2.52 at station 19a. Similar trends were
noted with the Brillouin diversity index. Benthic invertebrate diversities (Shannon-Weaver
index) calculated from Johnson's (1964) data ranged from 0.34 to 3.48. Weed and Rutschky
(1972) considered Shannon-Weaver diversities greater than 3.0 to represent unpolluted
conditions, a diversity of 1.0-2.0 moderately polluted, and a diversity of less than 1.0 severely
polluted.

48

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Table 1!

Number of taxa, total abundance (#/m^), and diversity indices (Shannon and
Brillouin) for all stations.

# of Taxa

Total
Abundance

Diversity

Station

Shannon

Brillouin

1

18

1,387

3.45

2.36

2

20

1,447

3.50

2.39

3

18

1,387

3.53

2.42

4

19

1,140

3.49

2.38

5

21

1,473

3.30

2.25

6

12

666

3.02

2.05

7

21

1,240

3.20

2.18

8

18

1,113

3.30

2.25

9

26

4,013

3.34

2.30

10

29

2,407

3.84

2.64

10a

28

2,093

3.91

2.68

11

27

1,394

3.96

2.70

12

16

634

3.08

2.10

13

22

1,300

3.49

2.38

14

23

1,447

3.07

2.09

15

24

2,360

3.29

2.26

16

19

2,380

3.10

2.13

17

22

1,793

3.17

2.17

18

24

2,793

2.57

1.76

19

22

2,700

3.16

2.17

19a

12

1,367

2.52

1.73

20

14

1,147

3.18

2.17

21

20

1,607

3.03

2.07

22

,27

5,900

2.83

1.95

23.

26

2,407

3.14

2.16

50

ii) Benthic-Commiinity ClassiFication

The benthic invertebrate communities were defined by means of cluster analysis. Based on the
total species composition at each station, the cluster analysis split the twenty-five sampling
locations into four groups or communities (1, 2, 3, and 4). The taxonomic composition of the
four communities is presented in Appendix VII. The cluster analysis using euclidean distance
and Ward's Method produced the best defined clusters (Figure 11).

Principal components analysis (PC A) was used to verify station groupings revealed by cluster
analysis (Figure 12). The PC A was completed on all the benthic invertebrate genera. The
component loadings and percent total variance for the principal components are presented in
Appendix VIII. Approximately 24 percent of the variation is explained by the first two factors.
Although the percent variation explained is relatively low, the PCA results generally confirm
those of the cluster analysis. All the stations from section A of the study area form a fairly
distinct group (community 1) in the PCA diagram. This group is characterized by relatively
high numbers of the Hexagenia, and the Coeloranypus sp. Communities 2, 3, and 4 revealed
by the cluster analysis is also fairly distinct in the PCA diagram. The stations found these
communities are influenced by the relative abundances of Hirudinea, Spirosperma ferox, and
immature tubificids, as indicated by their positive correlation with the first axis of the PCA axis.
Community 4 is separated from the other communities along the second PCA axis and is
influenced by the relative abundances of Polypedelium (Polypedelium) sp. and planaria.

51

Figure 11: Cluster analysis results using Euclidean distance and Ward's method. Large
numbers indicate groups of sites (small numbers) with similar benthic invertebrate

communities.

20-
19a-
12-
13-
,14-
16-
19-
18-
21-
17-
15-
11-
10a-
10-
9-
23-
22-

DIS.TANCES

5.00C

52

Figure 12; Scatterplot of sample locations on tiie first two principal components. Sites grouped
together have similar benthic invertebrate communities

X

o
i 0

-1

53

iii) Environmental Quality Evaluation

Figure 13 illustrates the separation in discriminant space of the four groups of stations defined
by cluster analysis and PC A. Correlations between sediment parameters and the first two
discriminant functions are given in Table 19.

The first discriminant axis (DA I) separates the communities characterizing the Welland River
sites (communities I, 2, and 3) from community 4, located in Chippawa Creek (Figure 13). The
axis indicates that communities 1, 2, and 3 are found in sediments with high concentrations of
metals such as chromium, copper, aluminum, lead, mercury, and arsenic relative to those
associated with community 4. The sediments of community 1, however are characterized by
lower levels of these metals relative to communities 2 and 3.

The second discriminant axis (DA II) separates community 1 from the remaining communities
in discriminant space (Figure 13). This axis indicates that community 1 is found in sediments
with slightly higher levels of aluminum and LOI relative to the sediments in communities 2, 3,
and 4.

This analysis suggests that the separation of communities is due to differences in concentrations
of sediment parameters. It indicates that communities 1, 2, and 3, located in the Welland River,
reflect degraded environmental conditions, relative to community 4 located in Chippawa Creek.
Of the Welland River communities, 2 and 3 are more degraded than 1. This observation is not
surprising, given the fact that communities 2 and 3 are located in urbanized sections of the river
which receive inputs from various industrial and municipal sources. Community 1, which
consists of all the stations in Section A of the river, may be in more organically enriched
sediments, as is illustrated by the relatively high loss on ignition (LOI). The only exception to
the general pattern of correspondence between contamination and community type is aluminum,
which is found in higher amounts in community 1 than in communities 2 and 3. The mean
concentrations of all sediment parameters associated with each community are presented in Table
20.

54

Figure 13: Plot of the benthic invertebrate communities in discriminant space as defined by the
first two discriminant functions.

O

i 2

V

< -4

1

4

1 1

2

2

2

2

1

4

2 2

2 2

3

3

1 3

3

-

1

1 1

-

1

1

1

1

1

1 1

1

15 -10

5 0
- DA I

5
-> Metals

10

55

Table 19: Correlations between sediment parameters and the first two discriminant functions
for benthic invertebrate communities.

Parameter

Discriminant Function
I II

Zinc

Cadmium

Copper

Lead

Chromium

Aluminum

Mercury

Arsenic

Loss on Ignition

Oil and Grease

m

0.163

-0.031

0.004

-0.064

0.218

0.121

0.142

-0.134

0.220

-0.258

0.244

-0.256

0.120

0.040

0.184

0.092

0.093

-0.453

0.014

-0.048

0.091

0.264

Table 20: Mean concentrations of sediment parameters associated with benthic invertebrate
communities. All units are expressed as //g/g, dry weight unless otherwise stated.

Benthic

Community

1

2

3

4

Parameter

Zinc

112.5

176.9

313.3

65.3

Cadmium

0.48

0.40

0.58

0.49

Copper

33.5

58.3

62.1

17.0

Lead

42.0

34.9

55.9

18.3

Chromium

43.1

156.8

73.6

20.8

Aluminum

32375

29182

30438

14075

Mercury

0.116

0.175

0.955

0.065

Arsenic

5.38

7.36

7.50

3.50

Loss on Ign.

10.09

4.00

5.25

5.50

Oil/ Grease

1500.6

1399.6

2198

1455

pH

6.98

7.23

7.08

7.00

56

To evaluate the Welland River environment by itself, community 4 was removed from the data
set and discriminant analysis was again performed. Figure 14 illustrates the separation in
discriminant space of the three Welland River communities. Correlations between sediment
parameters and the first two discriminant functions are given in Table 21. Results confirm
patterns observed in the discriminant analysis on the whole data set. However, they reveal
differences between conditions in which communities 2 and 3 are found.

The first discriminant axis (DA I) separates community 1 from communities 2 and 3 (Figure 14).
The axis indicates that communities 2 and 3 are found in sediments with higher concentrations
of metals such as chromium, copper, mercury, zinc, and arsenic relative to the sediments in
which community 1 exists. The sediments of community 1, however, are characterized by lower
levels of these metals, and higher LOI than those associated with communities 2 and 3. The
absence of high numbers of pollution-sensitive species such as the mayfly, Hexagenia sp. and
the presence of large numbers of Spirosperma ferox and immature tubificids in communities 2
and 3 could be due to high concentrations of various metals in the sediments.

The second discriminant axis (DA II) separates communities 2 and 3 in discriminant space
(Figure 14). This axis indicates that community i is found in sediments with slightly higher
levels of chromium, as well as a higher sediment pH, relative to community 3. Similarly
community 3 is found in sediments with higher mercury, lead, zinc, and LOI levels relative to
community 2.

The analysis suggests that communities 2 and 3 reflect degraded environmental conditions with
respect to various metals, relative to community 1. Community 2 and community 3 are located
in urbanized sections of the river which receive inputs from various industrial and municipal
sources. Community 1 , which consists of all the stations in Section A of the river, may be more
organically enriched, as illustrated by the high loss on ignition. Mean concentrations of all
sediment parameters associated with each community are presented in Table 20.

57

Figure 14: Plot of the Welland River benthic-invertebrate communities in discriminant space as
defined by the first two discriminant fiinctions.

2 0

4 -2 0
Cr,Cu,Hg,As,Zn,pH <

58

Table 21: Correlations between the sediment parameters and the first two discriminant
functions for the three benthic invertebrate communities in the Welland River.

Discriminant Function.

I

II

Parameter

Zinc

-0.144

0.186

Cadmium

0.033

0.128

Copper

-0.210

-0.013

Lead

0.009

0.192

Chromium

-0.282

-0.256

Aluminum

0.099

0.041

Mercury

-0.148

0.275

Arsenic

-0.169

-0.013

Loss on Ignition

0.402

0.200

Oil and Grease

0.031

0.088

m

-0.226

-0.240

59

Fisheries

The fish community of the Welland River is characterized by warmwater fish species including
catfish, carp, suckers, and freshwater drum (Appendix IX, Table 22). Salmonids are not
endemic. to the Welland River but are common in the Niagara River. Appendix IX also
compares the Welland River fish community with those of 12-Mile Creek and the Niagara River
area. All fish species caught in the Welland River during this survey are also found in the
Niagara River.

The most common fish species caught during the field surveys were channelcatfish (fall survey)
and white crappie (summer survey), both warmwater species. Substantially more fish were
caught in the hoop nets in section A than in Sections B and C (Table 23). A fisheries study by
Johnson (1964) found that the more! common fish included brown bullhead and sunfish (including
crappies). The author also noted a decrease in the number of fish in the area covered by
sections B, C, and D of the river.

During a twelve month survey by Steele (1981) on the Welland River, 25 species and two-
hybrids were caught (Appendix IX). Dominant fish species included white crappie, brown
bullhead, and channel catfish. Most of the species observed by Steele were tolerant of low
dissolved oxygen concentrations, and high turbidity.

60

Table 22: Fish species caught in the Welland River during the summer and fall surveys.

HOOP NET

Summer'

FalP

White Crappie^

25

2

White Bass

2

0

White Perch

0

10

Channel Catfish

0

59

Gizzard Shad

0

7

Freshwater Drum

0

8

White Sucker^

0

1

Yellow Bullhead

0

2

Shorthead Redhorse

0

Caip

0

1

Pumpkinseed"*

0

1

Rock Bass'

0

3

Seine net/Minnow traps

Summer

Fall'

Smallmouth Bass

-

1 Spottail Shiner

-

Emerald Shiner

*

Johnny Darter

-

Brook Silverside

-

Sculpin

¥

Banded Killifish

-

J

* - Fish species present (no numbers available)

1 - Three hoop-net sets - summer survey

2 - Two hoop-net sets - fall sur\'ey

3 - Fish species also caught in the seine net.

4 - No seining was conducted during the Fall Survey.

61

Table 23: Numbers of fish caught in hoop-net sets in sections A, B, and C.

HOOP NET

A

■ "

B

C

Total

White Crappie

23

2

0

27

White Bass

7

0

0

2

White Perch

10

0

0

10

Channel Catfish

59

0

0

59

Gizzard Shad

6

0

1

7

Freshwater Drunn

8

0

0

8

White Sucker

1

0

0

1

Yellow Bullhead

2

0

0

2

Shorthead Redhorse

1

0

1

2

Carp

1

0

0

1

Pumpkinseed

1

0

0

1

Rock Bass

0

0

3

3

Total

114

2

5

121

Aquatic Macrophytes

The Welland River shoreline throughout the study area was characterized by the presence of
several emergent aquatic macrophytes, particularly Typha latifolia and Sagiiiaria latifoUa (Table
24). Johnson (1964) and Dickman ei al. (1983) also noted an abundance of these species during
previous surveys.

Several studies have been completed regarding effects of industrial discharges on the macrophyte
community (Dickman and Haynes, date unknown; Dickman et al. , 1983). Dickman and Haynes
(date unknown) noted areas devoid of higher aquatic plants downstream of the previous 36"
Cyanamid outfall to the Welland River, as well as below the Thompson's Creek confluence.
The summer Tarandus survey also revealed an area below the Thompson's Creek confluence that
had sparse macrophyte growth; however the area below the previous outfall to the Welland River
now has a relatively luxuriant growth of macrophytes; this outfall was sealed in 1985. Dickman
and Haynes (Date unknown), also noted a similarly impacted zone downstream of the Atlas Steel
outfall. This impacted area was not observed during the summer survey by Tarandus personnel.
Several submerged aquatic macrophytes were also noted including Myriophyllum spicatum,
ValUsneria ame ricana, Ceratophyllum denwrsum, and Hcreramhera dubia (Table 24).

62

Submerged macrophytes noted by Johnson (1964) included Ceratophyllum demersum and
Potamogeton spp.. Dickinan et al. (1983) found that the submerged aquatic macrophytes were
dominated by Elodea canadensis, MyriophylUim sp. , Potamogeton pectinatus, and Ceratophyllum
sp. .

Table 24: Species of submergent and emergent aquatic macrophytes found in the study area
during the summer survey.

Common Name

Scientific Name

Abundance

Water Lily

Nymaphaea vaiiegatum

Common

Cattail

Typha latifolia

Common

Eurasian Milfoil

Mynophyllum s pi cat u m

Common

Smartweed

Polygonum sp.

Occasional

Wild Celery

Vallisneria amehcana

Common

Duckweed

Lemna sp.

Occasional

Bulrush

Scirpus sp.

Occasional

Arrowhead

Sagittaria latifolia

Common

Spiked Loosestrife

Lythrum salicaria

Occasional

Mud Plantain

Heteranthera dubia

Common

Pondweed

Potamogeton crispus

Rare

Pondweed

Potamogeton ricbardsonii

Rare

Coontail

Ceratophyllum demersum

Rare

Sedge

Carex sp.

Rare

Joe-Pie Weed

Eupatorium maculatum

Rare

Wild Rice

Zizania aquatica

Rare

Bushy Pondweed

Najas fle.xiUs

Rare

Waterweed

Elodea canadensis

Rare

63

Flow Measurements

Water velocities and depth were determined at cross-sections of the river in sections A, B, and
C. The flow calculations ranged from 19.24 mVs in section A to 37.12 mVs in section B, and
are presented in Appendix X. The flow estimate for section C was 25.09 mVs. Welland River
flow estimates cited in Acres (1990) ranged from 0 to 48 mVs.

The increased flows observed in section B are mainly the result of diversion of water from the
old Welland Ship Canal to the Welland River. The amount of water diverted from the old ship
canal has been estimated at 14.2 mVs (Acres 1990).

Flow in section C would normally be expected to be higher than that in section B because of
added diversion of canal water at Port Robinson and inputs from natural sources. During the
survey on November 9, 1990, however, the flow was found to be 25.09 mVs in this section, a
significant drop from that noted the previous day in section B. This apparent reduction in flow
may be the result of fluctuations of water flows in the Queenston-Chippawa Power Canal.
Reductions in flow in this facility have been known to temporarily "back up" and/or reduce the
flows in the lower sections of the Welland River (P. Odom, MOE, pers. com.).

64

Conclusions

Water Quality

1) Water quality parameters, including iron, copper and total phosphorus frequently exceeded
the PWQOs. Mercury concentrations at stations 1 and 2 exceeded the PWQO for this
metal. Between stations 1 to 5 there was a distinct and progressive decrease in mercury
levels in water. The elevated concentrations of mercury in the most upstream stations may
originate in the reservoir located upstream of the study area.

2) Most other water-quality parameters, including most metals, phenolics, total cyanide, PCBs,
PAHs, and organo-chlorine pesticides were generally below detection limits.

3) MOE monitoring data from several stations indicate that levels of zinc, copper, mercury,
chromium, and lead in Welland River water appear to have decreased from 1979 to 1987.
However, there has been a slight increase in the concentration of aluminum in the water
from 1981 to 1987.

Sediment Quality

1) Concentrations of several parameters including lead, chromium, mercury, cadmium, zinc,
iron, nickel, copper, arsenic, total kjeldahl nitrogen, total organic carbon, total phosphorus,
and PCBs exceeded the PSQG Lowest Effect Level at some stations. Consistently, stations
9, 10, 12, 18 and 19 had the most elevated concentrations of most of these parameters.
Station 9 is situated at a major storm water discharge, stations 10 and 12 are located in the
vicinity of the Atlas Steel plant and the Welland WPCP respectively, and stations 18 and
19 are located downstream of the Cyanamid Canada plant. Severe Effect Levels (SELs)
were also exceeded for chromium, iron, nickel and copper in the river from station 10
through at least station 19a. Mercury was only above the SEL at station 9; however,
mercury concentrations in the fall sediment sample at station 11 were equal to the SEL.
Levels of total cyanide and oil and grease also exceeded the QWDGs at some stations.

2) PAHs were also detected at several stations in the study area, with particularly high
concentrations noted at station 9. With the exception of trace amount's of PP-DDE, which
were detected at stations 6, 9 and 21, all organo-chlorine pesticides were below detection
limits. The more highly chlorinated furans were detected at stations 9, 15 and 21.
Concentrations of hexa- and hepta-chlorinated furans were highest at station 9. Sediments
at station 21 had the highest concentration of octachloro-dibenzofuran. Although the more
highly chlorinated dioxin and furan congeners such as octachlorinated forms are generally
believed to be less of an environmental concern than are the tetrachlorinated isomers, the
toxicity of these contaminants to aquatic biota is poorly understood at present.

65

3) Sediments in section D are relatively uncontaminated. The only water in this section is
diverted from the Niagara River to the Queenston-Chippawa Power Canal.

4) Sediments located in the western portion of section A are characterized by high levels of
total phosphorus, total kjeldahl nitrogen, and loss on ignition, probably due to the influence
of agricultural activities.

Benthic Invertebrate Community and Environmental Quality

1) Stations in section A, located upstream of the City of Welland, were characterized by
relatively high numbers of the pollution sensitive species Hexagenia sp. and Coelotanyus
sp. . These taxa were generally absent from stations in downstream sections. Stations in
sections B, C, and D were characterized by relatively high numbers of the more pollution
tolerant taxa Spirosperma ferox, Valvutu sp. , and Hydrobiidae, further substantiating the
relatively poorer quality of the sediments.

2) The total abundance of benthic invertebrates varied throughout the study area, ranging from
a low of 634 individuals per square meter at station 12 to a high of 5900 individuals per
square meter at station 22. Generally, stations located in sections B, C, and D had higher
total abundances than those found in section A, and in most cases were also characterized
by large number of oligochaetes.

3) Benthic invertebrate diversity (Shannon-Weaver and Brillouin Indices) varied more in
sections B, C, and D than in section A, where the indices were relatively constant. Almost
all diversity indices were greater than 3, which suggests that the study area represents
conditions that are relatively unpolluted.

4) Statistical analyses identified four separate benthic invertebrate communities, corresponding
to the four sections of the study area. The structure of each community was governed by
concentrations of certain sediment parameters. The benthic communities located in sections
A, B, and C (Welland River) were distinguished by their association with sediments which
had elevated concentrations of several metals (i.e. aluminum, chromium, copper, arsenic,
zinc, lead, mercury) relative to those in section D (Chippawa Creek). . The benthic
community of section A occurred in sediments with lower metal levels and higher loss on
ignition (organic content) relative to the other two Welland River communities (sections B
and C).

66

Fisheries

1) The fish community of the Welland River is dominated by warmwater fish species including
catfish, white crappie, carp, suckers, and freshwater drum. No salmonid species were
found, although they are common in the Niagara River. The fish community in section D
was not sampled.

2) Higher numbers of fish were caught in hoop-net sets in section A than in sections B and C.

Aquatic Macrophytes

1) The Welland River shoreline is dominated by several emergent aquatic macrophytes,
particularly Typha larifolia and Saginaria lafifolia. A number of submerged aquatic
macrophytes were also noted including Myriophyllum spicarum, VaUisneria americana, and
Cerarophyllum demersum. Sparse macrophyte growth was noted only below the
Thompson's Creek confluence.

67

References

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Dickman, M., C. Prescott, and K. L. E. Kaiser. 1983. Variations in the Aquatic Vegetation
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69

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70

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72

Appendix I

Water-Quality Graphics

Parameter

Page

Copper

74

Mercury

75

Aluminum

76

Iron, Zinc

77

Magnesium

78,

Total Phosphorus and

Total Kjeldahl

Nitrogen

79

Ammonia, Nitrite and Nitate

80

Parameter concentrations at each station sampled are indicated with shaded bars for
summer and fall sampling periods. Existing Provincial Water Quality Objectives
(PWQOs) are indicated with horizontal lines.

73

Copper (Summer)

PWQO

Station

Copper (Fall)

Station

Detection Limit = 5.0 ug/L
PWQO = 5.0 ug/L

Mercury {Summer)

0.35
0.30
0.25

_l 0.20

■>^
O)
^ 0.15

0.10

0.05

0.00

FI '

i:n

In
il

1

:V ■ ! -

PWQO

Station

Mercury (Fall)

PWQO

Station

Detection Limit = 0 . 05 ug/L
PWQO = 0.2 ug/L

Aluminum (Summer)

PWQO

Station

Aluminum (Fal

PWQO

■^c\JCo^^locû^^oocDO

Station

PWQO = 0 . 075 mg/L

Iron (Summer)

PWQO

Detection Limit = 0.01 mg/L
PWQO = 0.3 mg/L .

Station

Zinc (Summer)

PWQO

Station

Detection Limit = 10 ug/L
PWQO = 30 ug/L

Magnesium (Summer)

16.0

14.0

12.0

-I

10.0

E

8.0

6.0

4.0

2.0

0.0

-|

1
1

é

m

\

m

C\( 00 Tf «o

station

no PWQO available

Total Phosphorus (Summer)

Station

Detection limit = 0 . 001.4
PWQO = 0.03mg/L

Total Kjeldahl Nitrogen (Summer)

Station

no PWQO available

o

E
E

CO

c
o

O)

o

CD
03

■a

c:
CO

CD

CO
"c
o
E
E
<

JO

>
CO

<0

o
a

Appendix II
Sediment Quality Graphics

Parameter

Page

Lead

82

Chromium

83

Mercury

84

Cadmium

85

Arsenic

86

Zinc

87

Iron

88

Nickel

89

Copper

90

Aluminum ana

Magnesium

91

Loss On Ignition and

Total Organic

Carbon

92

Total Kjeldahl :

Nitrogen and

Total Phosphorus

93

Total Cyanide

94

Oil and Grease

95

Total PCBs

96

Parameter concentrations at each station sampled are indicated with shaded bars for
summer and fall sampling periods. Provincial Sediment Quality Guideline lowest
effect levels (LELs) are indicated with horizonal lines. Where concentrations
approach or exceed severe effect levels (SELs), these levels are also graphed. Open
Water Disposal Guidelines are indicated where Provincial Sediment Quality
Guidelines are not available.

Lead (Summer)

140
120
100 -

CD 80

^ 60

1 In

i H

L . .

pn

V-1-n

T

lfl..B.-,-._-

■p^jn4-

-i 1 - !

nnP^ ;.i

< ;-; j :J

LEL

y- c\t CO -rt m

Station

Lead (Fall)

140
120
100
80
60
40
20
0

LEL = 31 ug/g
SEL = 250 ug/g

-

-

l-]

I

1 (~j

m

-

n

- 1

\

rannn

\

^hS

r 1 1

1

--i-

"1

-'

- -i ;l-^-

-,\-

1 i""l

__j

J
--I

: 1

-1

J

1

ni i
■Mi 1

-A 1 "

1

i

A.

1 ,

LEL

Station

Chromium (Summer)

700

600

500

CD 400

=5 300

200

100

0

F^ni^FlF^f^FH^Hme

n

a

Hi

\m

ir'r-H-.JT-Ti

LEL

SEL

Station

Chromium (Fall)

f\JU

fïm

600
500
400

1

1

Fl

P^

300

-

f

^

r~|

■ 1
-. 1

1
1

i 1

|. j

-_\

1

200

- . ■ „

j

!

1

j

1
i

100

■H

i

--

-

LL

•-

-

i

-r

-'i

J--
1

4 - - -

n

r — — r-RriRfH

■- ■

--

\4

-f

—

--

-■

.-[

-i-

- 1

.J-..-.--'

LEL

SEL

Station

LEL = 26 ug/g
SEL= 110 ug/g

Mercury (Summer)

3.5

3

2.5

D5 2

O)

=3 1.5

1

0.5

-

'--- -il

: .:|-..|---..^|^-^f^^^^-^-^^

LEL
SEL

QU_X=^

03 CM CM CVJ CM

Station

Mercury (Fall)

3.5
3

2.5
2

1.5

1

0.5

LEL = 0.2ug/g
SEL = 2 ug/g

- in %

■ .....-[oij-l-L-i-iU

! it.il- i r— ! I -J ; : -1

LEL
SEL

Station

Cadmium (Summer)

1.60
1.40
1.20
1.00
O) 0-80
0.60
0.40 tt
0.20
0.00

-

■ i

L

i

a

s* ■-■1 - !

n"
.1

UZ
HmR

i -In

' ^nnn

zn^

Fl

LEL

c\j CO rr lo CD

Station

Cadmium (Fall)

1.60
1.40
1.20
O) 1.00
ZJ 0.80
0.60
0.40
0.20
0.00

-

■

1

fZ- ■

;

i j

i
-.1

- j
1

r î

1

z ■

i

1 1 '
1 r-'^

i '

1 1 :

1 , M, , ,

LEL

Station

LEL = 0.6ug/g
SEL= lOug/g

Arsenic (Summer)

LEL

Station

Arsenic (Fall)

18
16
14

O)

D) 10
8
6
4
2

-

f

m _m, _ ^ H'

- nn

lu 1
! 1 J

1

: 1

i ;

~]

il.' : 1 i

Il 1 1 .

. li il- ., .,, ,, w ,1 i , fi , , 1

LEL

Station

LEL = 6 ug/g
SEL = 33 ug/g

Zinc (Summer)

800

§^400

200

m

T

nnnr 1 1

J

LEL
SEL

Station

Zinc (Fall)

800

600

400 -

200

Station

LEL= 120ug/g
SEL = 820 ug/g

Iron (Summer)

120
100
80

O) 60

E

40
20

X

F:

r-

h

i

:-

i

*

LEL
SEL

Station

Iron (Fall)

120
100
D) 80
E 60
40
20

-

i — :

In

1

Inn

[Mn

M-Jr--

n-

inn

nnn ^

n

1 j

tt

Q

!

n

n

; j

V. \

-lii

1

i i -:

ijij j

. 1 "
=1

i 1 i

i
-j

LEL
SEL

Station

LEL = 2% (20 mg/g)
SEL = 4% (40 mg/g)

Nickel (Summer)

300

O) 200

100

F

1

FI ^

É---m

LEL
SEL

Station

Nickel (Fall)

400

300

=J 200

100

-

:

!

in

^-, ■

1

1

n

n

1
1

Ir-j
1 i

1 ;

! 1. '

r-

—j r^]

r-v-.-r-nnffl

Il i
-H-1

h

1 i

i

Il i

1 ! :

LEL
SEL

Station

LEL= 16ug/g
SEL = 75 ug/g

Copper (Summer)

160

nn

D) 100
50

r-^

pp

z

n "
- J .^

'n

1 --1

1

-.. i

n :-■!

zzbijjz

' : 1. i

Z-.Z^

i

-mm

.] .-Jl-.-il

LEL
SEL

Station

Copper (Fall)

150

100

50 h

f

1

1 f

I

npLi: .::

"i Zi ^ nZZZ
i 1 11 \r-iA i Z n ^

--3

, , , , H -HZ 1:1 "Ji-P .., ., ii i: :Zil.i! .1 ,1.. ; , i;Z , , 1

LEL.
SEL

Station

LEL= 16ug/g
SEL =110 ug/g

Aluminum (Summer)

40

30

D) 20

10

i -i n M [.! ir-i i nP

No LEL . SEL or OWDG available

Station

Magnesium (Summer)

Station

No LEL . SEL or OWDG available

Loss On Ignition (Summer)

c 10

o

°- 6

t]

;MJiad to toj

Rm

y w

Mm

n

ni

I

I : i t -I t-^^j t^"-1 1-^

-cv*», v<0<b^ 'ï>^.Ç>^^^^.5^^^^^^^cÇ>cvcO'o?

Station

no LEL . SEL or OWDG available

Total Organic Carbon (Summer)

12.0

10.0 -

c 8.0

o

qS 6.0

4.0

2.0

0.0

1:-"

1:

r'":"7'-""7'7

^-rr"":"'"m"":'""":":u"'

::-J

LEL

SEL

Station

LEL = 1 percent
SEL= 10 percent

Total Kjeldahl Nitrogen (Summer)

3.000

2.500

CD

2,000

1.500

1.000

500

F

1

■_ . r

' u ::

LEL

Station

LEL = 550 ug/g
SEL = 4.800 ug/g

Total Phosphorus (Summer)

2.500

2.000

1.500

500

LEL
SEL

Station

LEL = 600 ug/g
SEL = 2000 ug/g

Total Cyanide (Summer)

OWDG

1.5

i.O

0.5

Station

Total Cyanide (Fall)

OWDG

1.5

1.0

0.5 -

Station

OWDG = 0. 1 ug/g
Detection limit = 0. 05 ug/g

Oil and Grease (Summer)

Station

Oil and Grease (Fall)

12.000
10.000
8.000

O) 6.000

3

4.000

2.000

0

nnFlnnn

n

I

i[:in

OWDG

m

n

ra

Station

OWDG = 1 . 500 ug/g

Total PCB's (Fall)

0.16
0.14
0.12
0.10
0.08
0.06
0.04
0.02
0.00

"

•■'-i
i

f^

r

R-!

-^

- 1

1

1

"1

1 ^

i ^

1 i

1 , , , ,

^

1^

LEL

y- C\J CO -^ V) (O

Station

LEL = 0.07 ug/g

SEL cannot be calculated

Detection limit = 0 . 05 ug/g

Appendix III

Field observations of conductivity, dissolved
oxygen, and water temperature during the fall
survey.

97

November Survey
Conductivity /zmhos/cm

Station

North

Center

South

1

N/A

N/A

N/A

2

N/A

N/A

N/A

3

N/A

N/A

N/A

4

540

540

550

5

510

■530

530

6

500

500

500

7

500

500

505

8

540

500

500

9

450

400

400

10

425

430

425

10a

410

415

425

11

425

415

450

12

425

400

420

13

440

425

470

14

450

450

435

15

425

425

450

16

425

425

430

17

425

430

425

18

425

420

425

19

430

440

430

19a

450

450

450

20

475

450

450

21

450

450

450

22

310

315

360

23

340

325

325

98

November Survey - Temperature and Dissolved Oxygen |

North

Center

South 1

Station

Temp X

D.O.

mg/L

Temp °C

D.O. ■

mg/L

Temp °C

D.O.

mg/L

1

7.2

10.8

7.2

10.5.

7.9

10.3

2

7.5

10.2

7.8

10.0

7.5

10.2

3

7.5

10.2

7.9

10.1

7.7

10.1

4

6.9

8.6

7.0

8.4

7.0

8.4

5'

7.0

9.4

7.2

9.1

7.1

9.1

6

6.8

9.6

6.5

9.6

6.7

9.5

7

6.2

9.4

6.4

9.4

7.1

9.7

8

6.5

9.8

6.5

9.5

6.5

9.6

9

7.5

8.8

8.0

8.7

8.0

9.1

10

8.0

9.6

8.7

9.4

8.5

9.3

10a

8.2

9.2

8.5

9.4

8.7

• 9.3 •

11

8.0

9.7

8.0

9.7

8.5

9.6

12

8.5

9.6

8.3

9.5

8.8

9.4

13

8.2

9.2

8.3

9.5

8.5

9.5

14

8.5

9.8

8.5

9.6

8.5

9.6

15

8.5

9.3

8.1

8.3

8.1

8.3

16

7.5

8.8

7.5

8^7

8.1

8.6

17

8.4

8.9

8.1

8.9

8.4

8.7

18

8.0

8.8

8.0

8.8

8.2

8.8

19

8.0

8.8

7.9

8.9

8.0

8.9

19a

7.9

8.9

7.9

8.9

7.9

8.9

20

8.9

8.7

8.2

8.7

8.1

8.7

21

8.1

8.9

8.1

8.8

8.2

8.8

22

8.0

9.8

6.0

8.8

4.5

7.9

23

9.0

10.0

9.1

10.0

9.0

9.9

99

100

Appendix IV
Benthic Invertebrate Species List

101

INSECTA:
DIPTERA

Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C.) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C.) salinarius group

Chironomus (C.) staegeri group

Chironomus (C.) thummi group

Cladopehna sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:

Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
Djalmabatista sp.
Macropelopia sp.

Orthocladinae:

Diplocladius sp.
Paracricotopus sp.

102

Ceratopogonidae:
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:

Chaoborus sp.

EPHEMEROPTERA:
Ephemericlae:

Hexagenia sp.
Caenidae:

Caenis sp.

COLEOPTERA:

Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:

Sialis sp.

LEPTIDOPTERA

Pyralidae:

TRICOPTERA

Polycentropodidae:

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae:

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA

Coenagrionidae:

Enallagma sp.

103

OLIGOCHAETA:

Tubificidae:

Limnodrilus hoffmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

Naididae

Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

Lumbriculidae

NEMATODA: ■
PLANARIA:
HIRUDINEA:
HYDRACHNIDIA:

CRUSTACEA:
Amphipoda

Gammarus sp.

Hyalella sp.
Isopoda

Caecidotea sp.

MOLLUSCA:

GASTROPODA

Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae

104

Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA

Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

105

106

Appendix V
Benthic Invertebrate Species Counts

107

IC 2A 2B

Station
2C 3A 3E

3C 4A 4B 4C

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C.) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus. group

Chironomus (C. ) salinarius group

Chironomus (C.) staegeri group

Chironomus (C.) thummi group

Cladopelma sp.

Cryptochironomus sp. 2

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp 10

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp. 14

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp. 4

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
D jalmabatista sp.
Macropelopia sp.

12

6

4

3

5

4

44

6

4

6

8

8

8

5

4

7

2

15

10

8

3

14

4

6

10

9

6

2

20

21

6

8

5

3

Orthocladinae:
Diplocladius sp,
Paracricotopus sp.

Ceratopogonidae:
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:
Hexagenia sp.

Caenidae:
Caenis s

station
lA IB IC 2A 2B 2C 3A 38 3C 4A 48 4C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hydropsy chidae:

Cheumatopsyche sp.
Hydroptilidae:
• Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hoffmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

NADIDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

109

station
lA IB IC 2A 2B 2C 3A 3B 3C 4A 48 4C

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

3IVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

3 12 2 2

1

110

5C 6A 6B

Station
6C 7A 7E

INSECTA:
DIPTERA
Chironomidae :
Chironominae :

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C.) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
D jalmabatista sp.
Macropelopia sp.

11 10
6

Orthocladinae:
Diplocladius sp.
Paracricotopus sj

Ceratopogonidae :
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

Ill

station
5A 5B 5C 6A 6B 6C 7A 7B 7C 8A 80 8C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae:

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof fmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

63 19 13 7

3 13 95
2

28 41 13 23

NAD I DAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

station

6C 7A 7B 7C 8A

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

El VAL VA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

113

station
9C lOA lOB lOC IIA IIB IIC 12A 12E

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C. ) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C.) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae :
Apsectrotanypus sp.
Çoelotanypus sp.
Procladius sp.
Tanypus (Tanypus) s
Djalmabatista sp.
Macropelopia sp.

2 15
6 2 2 35 10 22

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae :
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

station
9C lOA lOB IOC llA IIB IIC 12A 12B 12C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae:

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae :

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp,
Leptoceridae:

Oecetis sp.

ODONATA
Coenagirionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof f meisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus mu'ltisetosus
Aulodrilus sp.
Tubificidae immature

64

40

5

64

12

2

1

4

2

7

11

2

4

1

1

6

1

80

32

3

7

10

52

5

1 10 10 10

1

NADIDAE
Pristinélla sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

LUMBRICULIDAE

Nematode:
Planaria:
Hirudinea:
Hydrachnidia

115

station
9A 9B 9C lOA lOB lOC IIA IIB IIC 12A 128 12C

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

1 6
1

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

1 16 2 7 3
3 19 3

BIVALVA
Sphaeriidae

Sphaerium sp. ■

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

13 22 6
1

16 18 2 2 7
3

station
13A 13B 13C 14A 14B 14C 15A 15B 15C 16A 168 16C

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis ) sf

(Chironomus) sp.
(C. ) anthracinus group
(C.) halophilus group
(C. ) plumosus group
(C. ) salinarius group
(C. ) staegeri group
(C. ) thummi group

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
Djairaabatista sp.
Macropelopia sp.

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae :
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

8 26 13 22
2

117

station
13A 13B 13C 14A 14B 14C ISA 15B 15C 16A 16B 16C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae:

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae :

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidaë
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hoffmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

12 42 35 36

NADIDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

2

1

1 1

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

118

station
13A 13B 13C 14A 14B 14C 15A 15B 15C 16A 16B 16C

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

31 7 2 14 20 16 13 13 2
5

2 7 9 19 17 6

5IVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

119

station
17A 17B 17C 18A 18B 18C 19A 19B 19C 20A 208 20C

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C.) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
Djalmabatista sp.
Macropelopia sp.

1

6

2

6

6

13

12

5

1

14

1

15

20

1

2

1

2

2

Orthocladinae:
Diplocladius sp.
Paracricotopus sj

Ceratopogonidae:
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae :

Hexagenia sp.
Caenidae:

Caenis sp.

120

17A 17B lie ISA li

Station

18C 19A 19B 19C 20A 20B 20C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae:

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae :

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof f meisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

2

1
1

4

3

26 137

65

6

52

63

NADIDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

121

station
17A 17B ne 18A 18B 18C 19A 19B 19C 20A 208 20C

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

Mollusca:
GASTROPODA
Vaivatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

13 17 6 6 27
1 1

10
63 13
22 21 34 9

BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorphe

6 6 9 5 4
2 2 3 2

5 20 4
1 2

122

station
21A 21B 21C 22A 22B 22C 23A 231

23C 24A 24B 24C

INSECTA:
DIPTERA
Chironomidae:
Chironominae:
Chironomini

Chironomus ( Chaetolabis ) sp.
Chironomus (Chironomus) sp.

(C.) anthracinus group
(C. ) halophilus group

plumosus group
salinarius group
staegeri group
thummi group

Chironomus

Chironomus

Chironomus (C. )

Chironomus (C.)

Chironomus (C. )

Chironomus (C. )

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

10

10
24 20
228 90 110 35

20 10 70

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
D jalmabatista sp.
Macropelopia sp.

2 12
1

1 7 12 36
1 2

2 4 2
2

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae :
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae :
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

123

station
21A 21B 21C 22A 22B 22C 23A 23B 23C 24A 248 24C

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGALOPTEFLA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae:

Cheumatopsyche sp.
Hydroptilidae :

Hydroptila sp.
Leptoceridae :

OecGtis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hoffraeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus mult isetosus
Aulodriius sp.
Tubificidae immature

NADIDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

1 5 2 22

2

2 6

14

35 3 1 9

26 24 22 30 54 33 29 9 83 25 3 21
2

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

3 2 12 1 1 7

124

station
21A 21B 21C 22A 22B 22C 23A 23B 23C 24A 24B 24C

sp.

Crustacea:
AMPHIPODA

Gammarus

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

10 5

1

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumig sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

10 34 7 14
9 4

1 6
38

125

station
25A 25B 25C

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C.) salinarius group

Chironomus (C.) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
Djalmabatista sp.
Macropelopia sp.

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae:
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

126

station
25A 25B 25C

COLEOPTERA:
Elmidae:

Dubiraphia sp.'
Dytiseidae:
Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hy dropsy c h idae:

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagr ion idae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof fmeisteri 22 2

L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox 1

Quistadrilus multisetosus

Aulodrilus sp. 12

Tubificidae immature 34 23 12

NAD IDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae 1.

LUMBRICULIDAE

Nematoda:

Planaria:

Hirudinea: 1

Hydrachnidia

127

station
25A 25B 25C

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp. .

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

128

Appendix VI

Benthic Invertebrate Species Abundances

129

station
5 6

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

27 20

173 13

60

27

40 13
100

133

133 40

113 173
53
53 60 33 13 67 93 53 80
40

13

7

53

7

13

27

7

53

13

7

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) s]
Djalmabatista sp.
Macropelopia sp.

80

67

80

40

13

93

333

120

140

87

27

87

53

7

213

167

133

113

127

127

140

133

133

140

127

20

33

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae :
Bezzia sp.
Culicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

7 20 13 13 27

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

80 80 233 180 127 27 107

130

Statron
12 3 4 5 6 7

COLEOPTEFIA:
Elmidae:

Dubiraphia sp.
Dytiseidae:
Coptotomus sp.

MEGALOPTEFIA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae :

Cheumatopsyche sp.
Hydr.optilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof fmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

NAD I DAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

40 7 7 7 33 13 13 7

7

47 140 67 100 153 133 107 180 727

13 80

13 47 13

40
7 33

180 340 247 260 547 133 460 293 767

LUMBRICULIDAE

Nematoda :
Planaria:
Hirudinea:
Hydrachnidia

131

station
123456789

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Catnbar idae

7 20 20 13 47

7
27 7 13

7 7 13 20 7 240

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps_

B I VAL VA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

40 20 60 107 113 13 33
7

132

station
12 13 14

INSECTA:
DIPTERA
Chironomidae:
Chironominae:

Chironomini

Chironomus ( Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C. ) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C.) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Poiydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

7

40

67
13

20
13

13

.00

120

67

13

93

27

13

20

40

20

133
27

40

113

167

13
107

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp,
Tanypus (Tanypus) S]
D jalmabatista sp.
Macropelopia sp.

53

93

40

13

60

67

267

27

73

13

13

7

87 407 180 207
13 40 20

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

13

67

3

3

133

40

Ceratopogonidae:
Bezzia sp.
Culicoides sp.
Mallochohelis s

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

13 7
7

33

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:

Coptotomus sp.

MEGfiLOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

Station
10 10a 11 12 13 14 15 16 17

TRICOPTERA
Polycentropodidae :

Polycentropus sp.

Cyrnellus sp.
Hydropsy chidae:

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hof fmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus multisetosus
Aulodrilus sp.
Tubificidae immature

7 33 53 253 613 40

7

133 160 7 200 20 20 47 7 7
47 33 7 7 40 33 13 107 7

460 327 33 93 373 627 753 607 567

NADIDAE
Pristinella sp.
P. sima
P. osborni
P. jenkinae
Pristina ? sp.
Nadidae

7

33

13

60

53

7

53
13

27

13

20

7

7

LUMBRICULIDAE

Nematoda:
Planaria:
Hirudinea:
Hydrachnidia

134

station
10 10a 11 12 13 14 15 16 17

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

20 47

7
20 60 7

i7 7 87 7 20

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculati
Lymnaeidae

Physa sp.

Stagn.icola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorphe

27 33 133 80 247 153 240 187 260
20 87 40

100 67 180 27 67 27 107 280 287
7

227 427 73 27 20 20 60 133 80
13
60 20 40 7 20 27

93 187 13

135

station
19a 20 21

INSECTA:
DIPTERA
Chironomidae :
Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

(Chironomus) sp.

(C.) anthracinus group

(C. ) halophilus group

(C. ) plumosus group

(C. ) salinarius group

(C.) staegeri group

(C. ) thummi group

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:
Apsectrotanypus sp.
Coelotanypus sp.
Procladius sp.
Tanypus (Tanypus) sp.
D jalmabatista sp.
Macropelopia sp.

57

67

293

2853

80
200

13
233

13

40

7

33

7

33

247

40

193

133

20

13

27

20

13

53

Orthocladinae:
Diplocladius sp.
Paracricotopus sp.

Ceratopogonidae :
Bezzia sp.
Cuiicoides sp.
Mallochohelis sp.

Chaoboridae:
Chaoborus sp.

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.

136

station
18 19 19a 20 21 22 23

COLEOPTERA:
Elmidae:

Dubiraphia sp.
Dytiseidae:
Coptotomus sp.

MEGALOPTERA
Sialidae:
Sialis sp.

LEPTIDOPTERA
Pyralidae:

TRICOPTERA
Polycentropodidae:

Polycentropus sp.

Cyrnellus sp.
Hydropsychidae:

Cheumatopsyche sp.
Hydroptilidae:

Hydroptila sp.
Leptoceridae:

Oecetis sp.

ODONATA
Coenagrionidae
Enallagma sp.

Oligochaeta:
TUBIFICIDAE
Limnodrilus hoffmeisteri
L. profundicola
L. angustipennis
L. claparedianus
L. sp.

Spirosperma ferox
Quistadrilus mult isetosus
Aulodrilus sp.
Tubificidae immature

307 360 160 73 53 253 233

27 27 7
7

20

13

7 13 53 93

20 47 7

7 80 60

1520 807 460 140 480 780 807

NAD I DAE
Pristinella sj:
P. sima
P. psborni
P. jenkinae
Pristina ? sp.
Nadidae

33 20

13
7

27
20 13

LUMBRICULIDAE

Nematode :
Planaria:
Hirudinea:
Hydrachnidia

13 7
40 27 47

.37

station
18 19 19a 20 21 22 23

Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
PODOCOPA
ISOPODA

Caecidotea sp.
DECAPODA

Cambaridae

20 100 27
7

Mollusca:
GASTROPODA
Valvatidae

Valvata sp.

V. tricarinata

V. sincera
Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha

80 193 53 180 93 7

13 13

67
507
287 433 260 267 20 7

127 193 60 93 340 100 47
33 20 60 280

7

13
7

138

Appendix VII

Taxonomic Composition of Benthic Communities
as defined by Cluster Analysis

Numbers are mean abundances (#/m^)

,39

Community

Invertebrate Taxa

1

2

3

4

DIPTERA

Chironomidae:

Chironominae:

Chironomini

12

I

3 ■

0

Chironomus (Chaetolabis) sp.

23

0

0

0

Chironomus (Chironomus) sp.

13

4

27

47

Chironomus (C.) anthracinus group

2

4

37

0

Chironomus (C.) halophilus group

3

■ 0

0

0

Chironomus (C.) plumosus group

3

1

0

0

Chironomus (C.) salinarius group

12

1

105

0

Chironomus (C.) staegeri group

22

0

0

0

Chironomus (C.) thummi group

14

2

77

0

Cladopelma sp.

7

2

0

0

Cryptochironomus sp.

53

66

68

37

Cryptotendipes sp.

5

0

0

33

Dicrotendipes sp.

1

2

20

153

Endochironomus sp.

2

1

0

1543

Glyptotendipes (Glyptotendipes) sp.

11

0

5

0

Microchironomus sp.

2

Ô

0

0

Parachironomous sp.

3

1

0

0

Paralauterboraiella sp.

0

0

0

40

Polypedilum (Polydelium) sp.

11

1

8

333

Polypedilum (Tripodura) sp.

12

0

0

0

Pseudochironomus sp.

2

0

0

3

Rheotanytarsus sp.

5

0

0

0

Tanytarsus sp.

9

0

0

33

Tanypodinae:

Apsectrotanypus sp.

47

19

47

0

Coelotanypus sp.

107

1

0

0

Procladius sp.'

144

157

160

330

Tanypus (Tanypus) sp.

57

12

7

0

Djalmabatista sp.

0

2

0

0

Macropelopia sp.

0

6

0

0

Orthocladinae:

0

0

20

0

Diplocladius sp.

0

0

8

0

140

Community

Invertebrate Taxa

Paracricotopus sp. 5 1 55 0

Ceratopogonidae:

Bezzia sp. 10 2 2 0

Culicoides sp. 12 0 0

Mallochohelis sp. 0 10 0

Chaoboridae:

Chaoborus sp. 5 10 0

EPHEMEROPTERA:
Ephemeridae:

Hexagenia sp.
Caenidae:

Caenis sp.
COLEOPTERA:

Elmidae:
Dubiraphia sp.

Dytiseidae:
Coptotomus sp.
MEGALOPTERA
Sialidae:

Sialis sp.

LEPTIDOPTERA
Pyfalidae:
TRICOPTERA

Polycentropodidae:
Polycentropus sp.
Cyrnellus sp.

Hydropsychidae:

Cheumatopsyche sp.

Hydroptilidae:
Hydroptila sp.

Leptoceridae:

Oecetis sp.
ODONATA

Coenagrionidae

Enallagma sp.

04

4

10

3

1

1

0

0

15 .

2

10

13

I

0

0

0

0

0

3

0

0 .

0

12

27

1

1

0

0

0

2

2

0

0

0

0

3

0

0

2

0

3

1

0

0

Invertebrate Taxa

Community

TUBIFICIDAE

Limnodrilus hoffmeisteri

L. profundicola

L. angustipennis

L. claparedianus

L. sp.

Spirosperma ferox

Quistadrilus multisetosus

Aulodrilus sp.

Tubificidae immature
NADIDAE

Pristinella sp.

P. sima

P. osborni

P. jenkinae

Nadidae

LUMBRICULIDAE
Nematoda:
Planaria:
Hirudinea:
Hydrachnidia
Crustacea:
AMPHIPODA

Gammarus sp.

Hyalella sp.
ISOPODA

Caecidotea sp.
GASTROPODA

Valvatidae

Valvata sp.

V. tricarinata

V. sincera

116

178

310

243

2

5

22

3

0

0

0

3

0

0

0

10

8

0

5

7

0

29

85

73

1

25

30

0

0

8

0

30

308

584

397

793

0

10

7

7

1

15

2

13

0

2

0

0

0

10

0

0

2

8

0

0

0

0

0

3

2

8

25

0

0

0

0

10

0

11

35

37

2

0

2

0

8

12

28

63

0

0

2

3

7

19

82

7

0

161

48

3

0

13

5

7

0

6

0

0

142

Community

Invertebrate Taxa

■ 1

2

• 3

4

0

46

0

0

2

186

87

14

Hydrobiidae

Hydrobiidae
Bithyniidae

Bithynia tentaculata
Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp.
Planorbidae

Gyralus sp.

Helisoma anceps
BIVALVA
Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp.
Corbiculidae

Corbicula sp
Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta
Dressenidae

Dreissena polymorpha 0 4 327

0

2

0

0

0

0

2

0

0

0

0

7

2

0

0

0

0 .

1

0

0

48

105

250

73

1

1

0

0

0

19

22

140

1

0

12

0

0

1

0

0

0

2

0

0

0

1

2

0

0

1

0

0

143

144

Appendix VIII

Component loadings and percent total variance explained for the PCA on benthic invertebrate
abundances

145

Appendix VIII: Component loadings and percent total variance for the PCA of the benthic
invertebrate abundances

Component Loadings

TAXA

Factor I

Factor II

Chironomini

Chironomus (Chaetolabis) sp.

Chironomous (Chironomous) sp.

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterbomiella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Apsectrotanypus sp.

Coelotanypus sp.

Procladius sp.

Tanypus (Tanypus) sp.

Djalmabatista sp.

Macropelopia sp.

Orthocladinae:

Diplocladius sp.

Paracricotopus sp.

Bezzia sp.

Culicoides sp.

Mallochohelis sp.

Chaoborus sp.

Hexagenia sp.

Caenis sp.

Dubiraphia sp.

Coptotomus sp.

Sialis sp.

Pyralidae:

Polycentropus sp.

Cymellus sp.

Cheumatopsyche sp.

Hydroptila sp.

Oecetis sp.

Enallagma sp.

0.337

0

364

0.459

0.

187

0.098

0

361

0.009

-0

127

0.083

-0

046

0.125

0

385

0.390

0

524

0.432

0

511

0.132

0

227

0.194

0

304

0.104

-0

005

0.350

0

381

0.263

0

639

0.339

0

172

0.134

0

579

0.447

0

304

0.141

0

463

0.335

-0

120

0.821

0

372

0.196

0

129

0.522

-0

182

0.069

-0

258

0.166

-0

369

0.009

-0

095

0.194

0

038

0.060

0

134

0.492

0

078

0.024

-0

230

0.069

-0

258

0.172

-0

056

0.631

0

288

0.024

0

128

0.197

0

602

0.417

0

124

0.094

-0

054

0.649

0

608

0.061

0

016

0.250

-0

149

0.403

0

506

0.257

0

182

0.548

0

151

0.194

0

038

I4(S

Appendix VIII: (continued)

TAXA

Componen

Lx)adin2S

Factor I

Factor II

L. sp.

0.484

0.282

Spirosperma ferox

0.668

0.032

Quistadrilus multisetosus

■ 0.380

-0.546

Aulodrilus sp.

0.359

0.094

Tubificidae immature

0.663

0.084

Pristinella sp.

0.493

-0.473

Pristina ? sp.

0.149

-0.222

Nadidae

0.085

-0.509

LUMBRICULIDAE

0.403

0.506

Nematoda:

-0.309

-0.044

Planaria:

0.542

0.637

Hirudinea:

0.806

0.099

Hydrachnidia

-0.293

0,237

Gammarus sp.

0.560

0.341

Hyalella sp.

0.438

0.406

Caecidotea sp.

0.247

0.085

Valvata sp.

0.444

-0.730

Hydrobiidae

0.472

-0.710

Bithynia tentaculata

0.115

-0.078

Physa sp.

0.069

-0.258

Stagnicola sp.

-0.094

-0. 054

Fossaria sp.

0.403

0.506

Gyralus sp.

-0.227

-0.028

Helisoma anceps

-0.028

-0. 158

Sphaerium sp.

0.418

-0.208

Musculium sp.

-0. 194

-0. 142

Psidium sp.

0.480

-0.305

Corbicula sp

-0.012

0.045

Unionidae

0.104

-0 . 299

Quadrula quadrula

0.142

-0.344

Ligumia sp.

0.305

-0.275

Dreissena polymorpha

0.537

-0.087

Percent Variance

12.791

10.687

147

148

Appendix IX

Fish Species found in the study area

149

Appendix IX: Fish species found in the study area

Lower Lower
Welland Welland
River' River^

Welland
River^

Welland 12-Mile
Rivei^ Creek^

Niagara
River*

White Crappie '^
White Bass
White Perch
Channel Catfish
Gizzard Shad
Freshwater Drum
White Sucker *

Yellow Bullhead
Shprthead Redhorse
Carp *

Pumpkinseed *

Rock Bass *

Smallmouth Bass
Spottail Shiner *
Emerald Shiner *
Johnny Darter *
Brook Silverside
Sculpin

Banded Killifish
Golden Shiner
Creek Chub
Blntnose minnow
Brown Bullhead
Tadpole Madtom
Mudminnow
Northern Pike
Black Crappie
Yellow Perch
Smelt

Bluegill Sunfish
Sea Lamprey
Brown Trout
Brook Trout
Hog Sucker
Northern Pearl Dace

150

Appendix IX - continued

Lower Lower

Welland Welland Welland Welland 12-Mile Niagara

River' River^ River^ River^ Creek^ River*

Redside Dace
Northern Redbelly Dace
Finescale Dace
River Chub
Blacknose Dace
Longnose Dace
Rosyface Shiner
Common Shiner
Brassy Minnow
Fathead Minnow
American Eel
Rainbow Darter
Fantail Darter
Brook Stickleback
Longnose Sucker
Silver Redhorse
River Redhorse
Black Redhorse
Greater Redhorse
Stonecat

Brindled Madtom
Black Bullhead
Lake Sturgeon
Longnose Gar
Bow fin
Alewife
Rainbow Trout
Lake Trout
Coho Salmon
Cisco

Lake Whitefish
Round Whitefish
Mooneye
Muskellunge
Lake Chub

151

Appendix IX - continued

Lower Lower

Welland Welland Welland Welland 12-Mile Niagara

River' River^ River^ River^ Creek^ River*

Blackchin Shiner

Blacknose Shiner

Spotfin Shiner

Sand Shiner

Mimic Shiner

Burbot

Threespine Stickleback

Ninespine Stickleback

Trout-Perch

Green Sunfish

Largemouth Bass

Sauger

Walleye

Iowa Darter

Least Darter

Log-Perch

Blackside Darter

Goldfish

Chain Pickerel

1 - Johnson, 1964

2 - Tarandus Associates Limited, 1990 - Summer and Fall field surveys

3 - Brindle ei al., 1988 - goldfish actually a carp/golfish hybrid
4- Steele, 1981

5 - Department of Commerce and Development, 1960

6 - Fish species thought to occur in the Niagara River area - Scott and Grossman, 1973

152

Appendix X

Flow calculations for sections A, B, and C.

153

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fr^

— ;^

==

^==

1

VO

*

o

I

1

s

0

VO

*

H

♦

—

*

*

fS

o

o

d

r-

(N

_

r-

1^

to

o

(N

d

r-i

d

d

d

u-,

u-)

o

c^

r-~

d

^

(N

od

00

d

d

^

>o

oo

2

^

o

u^

^.

d

M-

^

CNi

—

CN

d

(N

d

_

o

O

Ijn

d

00

"^

r^

iri

r-i

d

c^

d

m

^

u-,

d

ÎC

O

i^

iy-1

■*

^

VO

CN

(^

t^

d

d

TT

■^

VO

t-~

On

vO

^

[^

1^
od

d

s

j^

d

d

t~^

m

ir>

O

o

d

r-

00

VO

r»-]

od

oo

d

d

en

?

•^

u-i

cQ

ÏÏ

d

(^

oo

VO

o

o

d

d

S

S

o

d

S

ON

m

1V-)

o>

C^

r-j

-

d

d

Ol

VO

o

lo

m

d

o

.

o\

o
d

d

~

^

o

o

o

jC

—

>/-,

d

o

s

d

"

o
o
d

d

d

^

n

'e_

1

1
>

t

Z

o

5

o

i

<

o

5

=1-

s

00

>

IÎ

E

- o g

eu >
> <

.56

Appendix XI

Water Quality Data

157

Water and Sediment Parameter Abbreviations:

Abbreviation

Parameter

Pb

Lead

Zn

Zinc

Cd

Cadmium

Cr

Chromium

Fe

Iron

Se •

Selenium

As

Arsenic

Sb

Antimony

Ba

Barium

Be

Beryllium

Co

Cobalt

Cu

Copper

Mo

Molybdenum

Ni

Nickel

V

Vanadium

Ag

Silver

Hg

Mercury

CN

Cyanide

Mn

Manganese

Mg

Magnesium

AI

Aluminum

PCB

Polychlorinated biphenyls

OC

Organochlorine

PAH

Polycyclic Aromatic Hydrocarbons

NH4

Ammonia

TP

Total Phosphorus

TKN

Total Kjeldahl Nitrogen

NO2

Nitrite

NO3

Nitrate

TOC

Total Organic Carbon

LOI'

Loss on Ignition

SAR'

Sodium Adsorption Ratio

158

Water - Summer Survey

SITE

Zn

Cd

Mn

Co

Cu

Fe

Pb

Cr

mg/L

mg/L

mg/L

mg/L

mg/L

mg/L

mg/L

mg/L

1

<0.01

< 0.002

0.18

< 0.005

0.03

2.1

<0.01

< 0.005

2

<0.01

< 0.002

0.015

<0.01

< 0.005

3

<0.01

< 0.002

0.005

<0.01

< 0.005

4

<0.01

<■ 0.002

0.03

<0.01

< 0.005

5

<0.01

< 0.002

0.04

<0.01

< 0.005

6

<0.01

< 0.002

0.05

<0.01

< 0.005

7

<0.01

< 0.002

0.03

<0.01

< 0.005

8

<0.01

< 0.002

0.02

<0.01

< 0.005

9

<0.01

< 0.002

0.01

< 0.005

0.02

0.095

<0.01

< 0.005

10

<0.01

< 0.002

0.01

<0.01

< 0.005

10a

0.02

< 0.002

0.005

<0.01

< 0.005

11

<0.01

< 0.002

0.015

<0.01

< 0.005

12

<0.01

< 0.002

0.015

<0.01

< 0.005

13

<0.01

< 0.002

0.02

<0.01

< 0.005

14

<0.01

< 0.002

0.01

<0.01

< 0.005

15

<0.01

< 0.002

0.02

<0.005

0.005

0.43

<0.01

<0.005

16

<0.01

< 0.002

0.035

<0.01

< 0.005

17

<0.01

< 0.002

0.025

<0.01

< 0.005

18

<0.01

< 0.002

0.01

<0.01

0.0075

19

<0.01

< 0.002

0.03

• <0.01

< 0.005

19a

<0.01

< 0.002

0.005

<0.01

< 0.005

20

<0.01

< 0.002

0.01

<0.01

< 0.005

21

<0.01

< 0.002

0.01

< 0.005

0.015

0.4

<0.01

< 0.005

22

<0.01

< 0.002

0.0125

<0.01

< 0.005

23

<0.01

< 0.002

0.01

< 0.005

0.005

0.06

<0.01

< 0.005

159

Water - Summer Survey (Continued)

SITE

Ni

Be

Mo

V

A!

Ba

Hg

As

mg/L

mg/L

mg/L

mg/L

mg/L

mg/L

Mg/L

Mg/L

1

< 0.005

< 0.005

< 0.005

< 0.005

1.74

0.04

0.3

<5

2

1.42

0.25

<5

3

1.155

0.125

<5

4

0.97

0.1

<5

5

0.81

<0.05

<5

6

0.82

<0.05

<5

7

0.75

<0.05

<5

8

0.28

<0.05

<5

9

< 0.005

< 0.005

< 0.005

< 0.005

0.12

0.02

<0.05

<5

10

0.12

<0.05

<5

10a

0.13

<0.05

<5

11

0.11

<0.05

<5

12

0.1

<0.05

<5

13

0.3

<0.05

<5

14

0.28

<0.05

<5

15

< 0.005

< 0.005

< 0.005

< 0.005

0.36

0.02

<0.05

<5

16

0.24

<0.05

<5

17

0.3!

<0.05

<5

18

0.295

<0.05

<5

19

0.34

<0.05

<5

19a

0.32

<0.05

<5

20

0.3

<0.05

<5

21

< 0.005

< 0.005

< 0.005

< 0.005

0.32

0.02

<0.05

<5

99

0.16

<0.05

<5

23

< 0.005

< 0.005 ■

< 0.005

< 0.005

0.16

0.02

<0.05

<5

160

Water - Summer Survey (Continued)

SITE

Se

Ag

CN

Colour

Cond

Ammnia-N

Sb

Nitrite

Mg/L

mg/L

mg/L

TCU

uS/cm

mg/L

/^g/L

mg/1

1

<1

< 0.005

0.002

48

440

0.008

<2

0.003

2

0.002

440

3

0.002

415

4

0.002

420

5

0.002

360

6

0.002

350

7

0.002

310

8

0.002

290

9

<1

< 0.005

0.002

3

290

0.008

<2

0.005

10

0.002

290

10a

0.002

290

11

0.002

310

12

0.002

310

13

0.002

300

14

0.002

300

15

<1

< 0.005

0.002

4

290

0.008

<2

0.023

16

0.002

290

17

0.002

290

18

0.002

300

19

0.002

300

19a

0.002

300

20

0.002

310

21

<1

< 0.005

0.002

4

300

0.33

<2

0.04

22

0.002

280

23

<1

< 0.005

0.002

9

290

0.23

<2

0.003

Water - Summer Survey (Continued)

SITE

Mg

Nitrate

pH

Phenolics

TKN

ss

Turb

TP

mg/L

mg/L

-log[Hn

mg/L

mg/L

mg/L

NTU

mg/L

1

14.1

0.35

8

0.01

1

48

6.5

0.2

9

7.9

0.012

1.01

5.5

0.25

3

7.95

0.0025

0.955

7.3

0.1515

4

7.95

0.029

0.81

6.8

0.149

5

8.05

<0.001

0.62

4.3

0.098

6

8

0.004

0.56

4.2

0.083

7

8.15

0.004

0.43

1.8

0.053

8

8.1

<0.001

0.33

0.5

0.024

9

8.5

0.16

8.125

0.012

0.42

7

0.3

0.016

10

8.1

0.012

0.28

0.3

0.016

10a

8.2

0.001

0.3

0.3

0.013

11

8.25

0.002

0.33

0.8

0.066

12

8.15

0.001

0.4

1.1

0.064

13

8.15

0.022

0.38

0.7

0.044

14

8.1

0.03

0.4

0.8

0.045

15

8.9

0.31

8.1

0.024

0.39

14

0.5

0.041

16

8.05

0.016

0.37

0.5

0.042

17

8.1

0.031

0.34

0.4

0.042

18

8.45

0.008

0.33

0.55

0.048

19

8.15

0.002

0.39

0.6

0.053

19a

8.15

0.004

0.46

0.6

0.053

20

8.1

0.022

0.4

0.6

0.052

21

9.2

0.55

8.15

0.016

2.6

14

0.5

0.06

22

8.4

0.0015

0.315

0.3

0.0135

23

8.4

0.16

8.25

0.005

0.39

4

0.3

0.013

162

Water - Fall Survey

SITE

Cu

Al

Hg

Phenols

mg/L

mg/L

Mg/L

mg/L

1

0.005

1.85

<0.05

<0.001

2

0.01

2.7

<0.05

<0.001

3

0.005

3.4

<0.05

<0.001

4

0.01

1.03

<0.05

<0.001

5

0.005

0.86

<0.05

< 0.001

6

0.005

1.9

< 0.001

7

0.005

1.91

<0.001

8

0.005

1.14

<0.001

9

< 0.005

1.49

<0.001

10

0.01

0.54

<0.05

<0.00I

10a

<0.001

11

<0.001

12

<0.001

13

<0.001

14

<0.001

15

0.01

1.3

<0.05

<0.001

16

<0.001

17

<0.001

18

< 0.001

19

<0.001

19a

<0.001

20

<0.001

21

< 0.005

1.07

<0.05

<o.oor

22

<0.001

23

0.035

0.34

<0.05

<0.001

163

164

Appendix XII

Sediment Quality Data

165

Sediments - Summer Survey

SITE

CN

LOI

O&G

phenolics

PH

Zn

Cd

TOC

Mg/g

%

Mg/g

Mg/g

-log[H^]

Mg/g

Mg/g

%

1

0.13

14

2900

0.01

6.8

116

0.6

7.4

2

<0.05

11

1040

0.01

7

97

0.5

3

<0.05

12

980

0.01

6.9

116

0.45

4

0.075

10.5

845

0.01

6.95

104

0.425

5

<0.05

12

1070

0.02

7

108

0.55

6

<0.05

7.2

870

0.01

7.3

112

0.4

7

<0.05

7

1800

0.01

6.9

135

0.55

8

<0.05

7

2500

0.01

7

112

0.4

9

<0.05

7

4550

0.01

7

335

0.8

3.55

10

<0.05

7

2000

0.01

7

550

0.975

"lOa

<0.05

5

1990

0.01

7

270

0.4

11

<0.05

2

250

0.01

7.3

98

0.15

12

<0.05

6

3200

0.01

7.1

620

1.4

13

<0.05

2

195

0.01

7.5

75

0.25

14

<0.05

2

320

0.01

7.5

76

0.1

15

<0.05

2

410

0.01

7.3

83

0.15

0.92

16

<0.05

4

1110

0.01

7.1

116

0.2

17

<0.05

5

1670

0.01

7.2

163

0.35

18

0.09

5

3100

0.01

7.1

191

0.5

19

<0.05

5

2500

0.01

7.1

330

0.9

19a

<0.05

5

750

0.01

7.2

127

0.25

20

0.18

5

1280

0.01

7.2

69.5

0.1

21

0.1

3

860

0.01

7.2

95

0.2

1.13

22

<0.05

5

1240

0.025

7

75.5

0.675

23

<0.05

6

1670

0.01

7

55

0.3

2.5

166

Sediments - Summer Survey (Continued)

SITE

SAR

TKN

Mn

Co

Cu

Fe

Pb

Cr

Ni

Be

Mg/g

/^g/g

Mg/g

Mg/g

Mg/g

Mg/
g

Mg/g

Mg/
g

A^g/g

.

1.14

2800

580

14.5

35

32000

49

40

33

1.5

2

24

26

40

3

33

37

49

4

29

31

43.5

5

31

34

43

6

30

34 ■

40

7

35

85

45

8

51

40

44

9

0.76

1910

430

10.75

93.5

30000

74.5

55.5

54

1

10

77

86

95

10a

50

38

91

11

28

25

53

12

85

62

260

13

34

21

162

14

26

22

79

15

0.83

290

960

■ 19

47

58000

26

300

178

I

16

31

23

43

17

58

50

300

18

64

45.5

265

19

115

41

107

19a

33

24

59

20

54.5

40.5

53

21

0.8

800

650

13

94

35000

29

97

75

1

. 22

19

20.5

22.5

23

0.9

1340

330

6.5

15

16400

16

19

19.5

0.5

167

Sediments - Summer Survey (Continued)

SITE

Mo

V

Al

Mg

Ba

Hg

Ag

Sb

TP

As

Mg/g

/^g/g

Mg/g

Mg/g

Mg/g

Mg/g

/^g/g

Mg/g

/^g/g

/ig/g

1

0.5

58

34000

9400

139

0.08

0.5

1

1020

5

2

33000

0.04

5

3

38000

0.12

7

4

34000

0.07

5

5

32000

0.06

5

6

31000

0.06

5

7

31000

0.1

6

8

26000

0.4

5

9

1.75

34.5

17750

15900

102.5

2.22

0.5

1

1005

5

10

34000

0.18

11

10a

35000

1.4

8

11

35000

0.02

6

12

38000

0.68

17

13

29000

0.02

6

14

29000

0.02

6

15

24

42

23000

13900

118

0.06

0.5

1

1060

6

16

32000

0.28

6

17

31000

0.1

6

18

22000

0.28

6.5

19

38000

0.26

10

19a

28000

0.08

6

20

25000

0.04

5.5

21

3.5

43

26000

14000

127

0.1

0.5

1

1300

6

22

15750

0.07

4

23

0.5

27

12400

17200

51

0.06

0.5

1

620

3

168

Sediments - Fall Survey

SITE

PCBs

Hg

Zn

Cd

CN

O&G

/^g/g

A^g/g

Mg/g

/^g/g

Mg/g

Mg/g

1

<0.05

<0.05

960

n

0.15

670

3

<0.05

■

1570

4

540

5

<0.05

130

0.4

720

6

112

0.6

970

7

0.13

0.36

177

0.9

2700

8

0.074

1.64

125

0.6

1660

9

0.11

3.11

309

0.7

4850

10

0.045

1.3

310

0.7

3600

10a

0.14

142

0.3

780

11

2

280

0.8

3400

12

0.92

570

1.5

11800

13

0.04

99

0.2

450

14

137

0.25

515

15

0.051

192

0.5

2000

16

187

0.6

1320

17

210

0.7

0.13

2600

18

210

0.6

0.15

2600

19

220

0.7

0.1

2700

19a

<0.05

6600

20

179

0.6

1.67

1560

21

0.142

0.12

3550

22

<0.05

1120

23

<0.05

1080

,69

Sediments - Fall Survey (Continued)

SITE

Mn

Co

Cu

Fe

Pb

Cr

Ni

As 1

/^g/g

Mg/g

Mg/g

/^g/g

Mg/g

Mg/g

Mg/g

Mg/g 1

5

850

15

31

38000

38

50

38

6

680

12.5

34

32000

36

43

34

7

570

12

72

29000

73

46

• 37

5

8

630

12

94

28000

47

49

41

5

9

615

13.3

109.5

35000

93.5

188.5

131

5

10

1210

38

168

118000

87

670

390

11

lOa

810

16.5

43

52000

38

149

98

11

740

18.5

73

53000

63

250

166

4

12

730

23

105

70000

91

460

270

10

13

980

17

52

60000

23

300

179

6

14

995

19

53.5

59000

28.5

385

230

6.5

15

940

18

66

54000

48

340

177

8

16

990

19.5

71

63000

44

420

240

5

17

960

20

71

59000

49

440

230

7

18

840

19

74

53000

49

380

210

5

19

840

19

116

54000

53

350

192

7

20

820

22

138

47000

80

260

192

8

170